Oceanological and Hydrobiological Studies - PTHpth.home.pl/pobierz/Oceanological_and_Hydrobiological... · 2008-08-03 · Vol. XXXVI Supplement 4 2007 Oceanological and Hydrobiological

Vol. XXXVI Supplement 4

2007

Oceanological and Hydrobiological

Studies

“Studies on benthic macroinvertebrates -

Environmental and anthropogenic aspects” Institute of Oceanography University of Gdańsk

Oceanological and Hydrobiological Studies Quarterly journal published by the Institute of Oceanography of the University of Gdansk

Editor-in-Chief: Marcin Pliński Editorial Secretary: Grzegorz Kozłowski

English editorial advisory: Jennifer Zielińska

Galileo

Editorial Advisory Board

Lubomira Burchardt (Poland), Juri Elken (Estonia), Pertti Eloranta (Finland), Carlo Heip (The Netherlands), Halina Piekarek-Jankowska (Poland), Barbara Kawecka (Poland), Erkki Leppäkoski (Finland), Harold G. Marshall (USA), Stanisław Massel (Poland), Stanisław Musielak (Poland), Alice Newton (Portugal), Sergej Olenin (Lithuania), Anto Raukas (Estonia), Anna Szaniawska (Poland), Piotr Szefer (Poland), Brian A. Whitton (England)

www.oandhs.org e-mail address:

[email protected]

The Address of the Editorial Office:

Institute of Oceanography, University of Gdańsk al. Marszałka Piłsudskiego 46 p. 698, 81-378 Gdynia, Poland

Phone/fax (Int + 48 58) 523-68-98

ISSN 1730-413X eISSN 1897-3191

Copyright© by Institute of Oceanography, University of Gdańsk

Printed by IO UG, 2007 Volume of hard copy format distribution: 150 copies per issue

Content

IZABELA CZERNIAWSKA-KUSZA Scientific problems and history of benthological workshops 5 IRENA BIELAŃSKA-GRAJNER Comparison of psammon rotifers community in lakes of Northwestern

Poland and artificial reservoirs of Upper Silesia

7 ELŻBIETA DUMNICKA Distribution of Oligochaeta in various littoral habitats in the

anthropogenic reservoirs

13 BARTŁOMIEJ GOŁDYN , SZYMON KONWERSKI, JERZY BŁOSZYK Large branchiopods (Anostraca, Notostraca, Spinicaudata, Laevicaudata)

of small, astatic waterbodies in the environs of Poznań (Wielkopolska Region, Western Poland)

21 IZABELA JABŁOŃSKA–BARNA Macroinvertebrate benthic communities in the macrophyte-dominated

Lake Łuknajno (northeastern Poland)

29 IGOR JATULEWICZ Comparison of macroinvertebrate communities associated with various

habitats in anthropogenic reservoirs

39 LUCYNA KOPROWSKA, IZABELA JABŁOŃSKA–BARNA Biomonitoring of the Łyna River (North Poland) in the years 1974-2006 on

the basis of the benthic macroinvertrates in the presence of Cyclotella meneghiniana and Nodularia spumigena

49 MAŁGORZATA KORYCIŃSKA, ELŻBIETA KRÓLAK The effect of selected environmental factors on the occurrence of

macroinvertebrates in the Osownica River

55 ELŻBIETA KRÓLAK, MAŁGORZATA KORYCIŃSKA, ALEKSANDRA MICHALUK The influence of the sewage treatment plant in Międzyrzec Podlaski on the

Krzna River (eastern Poland) water quality

63 ROBERT STRYJECKI The role of fish ponds as important habitats for water mites

(Hydrachnidia, Acari)

73 MARIUSZ TSZYDEL, MARIA GRZYBKOWSKA, MICHAŁ KURZAWSKI, NINA KALISIAK Response of riverine benthofauna associated with gravel-pebble bottom to

impoundment – interhabitat comparison

81 BARBARA WOJTASIK, JAROSŁAW KUR Size differences between individuals of Nannopus palustris Brady, 1880

(Crustacea, Harpacticoida, Huntemannidae) from tidal flats on Spitsbergen

97

JANUSZ ŻBIKOWSKI Various reproductive strategies of two species of Oligochaeta: Limnodrilus

hoffmeisteri and Tubifex tubifex

109

PAWEŁ ZDOLIŃSKI, MAGDALENA LAMPART-KAŁUŻNIACKA Biological monitoring of the surface Pomeranian rivers (North Poland) on

the basis of the macroinvertebrates

119

SCIENTIFIC PROBLEMS AND HISTORY OF BENTHOLOGICAL WORKSHOPS

On May 17-19, 2007, the XIV Benthological Workshop on the subject „Hydromorphological assessment of water ecosystems” was held in Turawa, Opole Region in southwestern Poland. The meeting was organized by the Department of Land Protection of the University of Opole and by the Benthological Section of the Polish Hydrobiological Society.

The workshop schedule was divided into two parts, namely theoretical and practical ones. The main aims of the first part were: (1) presentation and discussion of the research trends and current surveys of freshwater zoobenthos, (2) presentation of the River Habitat Survey (RHS) system, which is defined as “ecological status and classification of running water ecosystems” according to the EC Water Framework Directive. The RHS system was carried out as a field training to recognize the hydromorphological approach in river ecosystem classification. Additionally, a laboratory training was performed on caddies-flies (Trichoptera) identification.

More than 60 participants from most of the hydrobiological research centers in Poland actively attended the Workshop. During the meeting, one plenary lecture on the RHS method/system as well as 14 oral communications and 31 posters within the scope of benthic fauna were presented. The majority of presentations focused on two general themes: (1) biodiversity and distribution of benthic assemblages/communities as well as individual taxa (e.i. Oligochaeta, Ostracoda, Ephemeroptera, Trichoptera, and Gastropoda) in relation to habitat of the freshwater ecosystems, (2) benthic macroinvertebrates as indicators of current status and changes in quality of water environment. A few presentations concerned the fish pressure on macroinvertebrates.

The present volume contains 13 papers illustrating problems, which were presented and discussed during the Workshop.

History of the Benthological Workshops

A Benthological Workshop is an annual meeting of research workers interested in bottom fauna surveys, which has been organized by various Polish scientific centers since 1994. The Workshops took place on the initiative of the Benthological Section of the Polish Hydrobiological Society, established during the XV Polish Hydrobiologists Meeting in Gdynia in 1992 year. The first board of the Section was represented by Andrzej Kownacki (chairman), Małgorzata Kłonowska-Olejnik and Ryszard Kornijów (members), and was also the organizer of the first Workshop. Its aim was to integrate hydrobiologists interested in benthic invertebrates, exchanging of scientific information, and

expanding practical usage of researches on zoobenthos in evaluation of water enviroment.

Chronological order of the Benthological Workshops:

• I Workshop – Zakopane, 20-21 May 1994, entitled “Structure, functioning and protection of mountain water ecosystems”, organizers: M.Kłonowska-Olejnik (Jagiellonian University in Kraków) and R. Kornijów (Agricultural University in Lublin).

• II Workshop – Piaseczno, 2-3 June 1995, “Ecology of water ecosystems of Polesie Lubelskie”, chairman of an organizing committee: R.Kornijów (Agricultural University in Lublin).

• III Workshop – Lidzbark Welski, 14-15 September 1996, “Using of bottom fauna in biomonitoring of running waters in Poland”, chairman: Lucyna Koprowska (University of Warmia and Mazury in Olsztyn, former University of Agriculture and Technology).

• IV Workshop – Siedlce, 5-7 June 1997, “Bottom fauna of small freshwater bodies and streams”, chairmen: Teresa Nesteruk and Beata Jakubik (University of Podlasie in Siedlce, former Higher Teacher Training School).

• V Workshop – Bromierzyk, 4-7 June 1998, “Hydrobiological studies of small water bodies”, chairmen: Grzegorz Tończyk and Małgorzata Klukowska (University of Łódź).

• VI Workshop – Ojców, 27-29 May 1999, “Fauna of carst surface water and underground water”, chairmen: Elżbieta Dumnicka and Joanna Galas (Karol Starmach Department of Freshwater Biology, Polish Academy of Sciences in Kraków).

• VII Workshop – Jeziory, 25-27 May 2000, “Benthic fauna of lakes”, chairman Piotr Domek (Adam Mickiewicz University in Poznań).

• VIII Workshop – Mikołajki, 9-12 May 2001, “Mazovian Great Lakes, threat and protection”, chairman: Andrzej Kołodziejczyk (University of Warsaw).

• IX Workshop – Toruń-Bachotek, 15-17 May 2002, “Benthic fauna of shallow lakes”, chairman: Janusz Żbikowski (Nicolaus Copernicus University in Toruń).

• X Workshop – Poznań-Ciążeń, 8-10 May 2003, “Studies on benthic fauna in various water types”, chairman: Piotr Domek (Adam Mickiewicz University in Poznań).

• XI Workshop – Jastrzębia Góra-Gdańsk, 6-8 May 2004, “Biodiversity of a bottom environment of water bodies”, chairman: Tadeusz Namiotko (Unviersity of Gdańsk).

• XII Workshop – Warszawa-Giżycko, 12-14 May 2005, chairman: Andrzej Kołodziejczyk (University of Warsaw).

• XIII Workshop – Ochotnica-Kraków, 18-20 May 2006,”The application of hydrology to biological studies of running waters”, chairman: Małgorzata Kłonowska-Olejnik (Jagiellonian University in Kraków).

• XIV Workshop – Opole-Turawa, 17-19 May 2007, “Hydromorfological assessment of water ecosystems”, chairman: Izabela Czerniawska-Kusza (University of Opole).

O c e a n o l o g i c a l a n d H y d r o b i o l o g i c a l S t u d i e s I n t e r n a t i o n a l J o u r n a l o f O c e a n o g r a p h y a n d H y d r o b i o l o g y

Vol. XXXVI, Supplement 4

Institute of Oceanography ISSN 1730-413X

(7-12) 2007

University of Gdańsk eISSN 1897-3191

Copyright© by Institute of Oceanography, University of Gdańsk, Poland www.oandhs.org

Comparison of psammon rotifers community in lakes of Northwestern Poland and artificial reservoirs of

Upper Silesia

Irena Bielańska-Grajner1

Department of Ecology, University of Silesia Ul. Bankowa 9, 40-007 Katowice, Poland

Key words: psammon, rotifers, lakes, reservoirs

Abstract

The aim of this paper was to show differences and similarities among of the rotifers communities in artificial reservoirs and natural lakes. The studies were carried out in 9 lakes of different trophy in Northwestern Poland and 9 artificial reservoirs in the Silesian Upland. The samples were collected in spring, summer and autumn 2001 and 2002.

To evaluate differences in species structure of rotifer fauna between lakes and artificial reservoirs, the species diversity as well as index of faunal originality (IFO) and evenness were used. Similarities of rotifer communities were calculated with modified index of Morisity.

Statistically not significant differences were found between lakes and reservoirs in evenness and species diversity indexes H’, PIE and faunal originality index.

According to Morisity index (which designates similarity structure of dominant community only by taking into consideration the species of very high abundance), three classes of reservoirs were distinguished. The first class included all lakes and one dam reservoir Kozłowa Góra. The second one was represented by two reservoirs, Paprocany and Pogoria III, and the others artificial reservoirs were qualified to the third class.

1 e-mail: [email protected]

Original research paper Received: Accepted:

July 05, 2007 November 19, 2007

I. Bielańska-Grajner

Copyright© by Institute of Oceanography, University of Gdańsk, Poland

8

INTRODUCTION

The first investigations of psammon rotifers in Polish lakes were carried out by Wiszniewski (1934, 1947). The community structure of psammon rotifers in Masurian lakes with different trophy was studied by Ejsmont-Karabin (2003). She determined the community composition and abundance of psammon rotifers related to trophy state of lakes and grain-size structure of sand. In turn, the investigations on psammon rotifer communities in the water bodies of South-Eastern Poland were carried out by Radwan and Bielańska-Grajner (1998, 2001). A few information concerns psammon rotifers in artificial reservoirs (Bielańska-Grajner 2001, 2004, 2005).

Community structure and abundance of psammon communities of Rotifera in relation to algae, porosity, grain-size structure of sand, and size of sand beach were studied in some lakes in Northwestern Poland and some artificial reservoirs in Silesian Upland (Bielańska-Grajner 2005).

The aim of this paper was to show differences and similarities of the rotifer communities in natural lakes and artificial reservoirs.

MATERIALS AND METHODS

Rotifers were collected during 2001 and 2002 from 9 lakes located in Northwestern Poland and 9 artificial reservoirs in Silesian Upland (Table 1).

The samples of psammon were taken from three zones of arenal (hydroarenal, hygroarenal, euarenal). They were collected with a plastic sharp-edged corer, 3.5 cm in diameter at five points of each zone. The number of rotifers was expressed per 1 dm3 of wet sand.

Statistical analyses

Evenness and species diversity the Shannon-Weaver (Krebs 1989), species diversity Hurlbert PIE [1] (Lampert, Sommer 1996) and index of faunal originality IFO (Puchalski after Ejsmont-Karabin 1995) [2] were used. Similarity of rotifer communities was calculated using modified index of Morisity (Mo) (Horn 1966) [3]:

( )∑−+= 21

1 ipN

NPIE

[1]

smIFO

∑=

1

[2]

Comparison of psammon rotifers community in lakes and artificial reservoirs

www.oandhs.org

9

∑ ∑

∑

= =

=

+= n

a

n

aaa

n

iii

yx

yxMo

1 1

22

1

2

[3]

Comparison of mean values of species diversities H’, PIE and IFO between

natural lakes and artificial reservoirs was done using t- Student test; α = 0.05 (Statistica 5.1PL).

RESULTS AND DISCUSSION

The number of species in the lakes and reservoirs under study ranged from 13 to 57 (Table 2). In total, in the lakes from 1422 to 96 641 ind. dm-3 and in the reservoirs from 12 178 to 154 704 ind. dm-3 of sand were collected.

In the studied lakes and reservoirs diversity index of Shannon-Weaver (min. 0.6 – max. 2.92) was lower than that (min. 0.0 – max 3.3) reported by Ejsmont-Karabin (2003).

Table 1

Selected morphometric and ecological parameters of lakes and reservoirs: size of psammolitoral: little – 1 m width, to 3 m length; mean – 3 m width, 15 m length; large – 8 m width, 40 m length and more; eu – euarenal, hyd – hydroarenal; mean temperature, oxygen, pH, phosphate in 2001-2002

Parameters

Surface[ha]

Size of psammolitoral Temperature[oC] pH Oxygen

[mgO2 dm-3]Phosphate

[mgPO4 dm-3] eu hyd eu hyd eu hyd eu hyd Bytowskie Lakeland Jeleń 84 large 11 14.2 7 7.1 3.8 8.33 0.66 0.17 Drawskie Lakeland Sarcze 35.5 mean 14.8 16.6 7.5 8.5 3.93 9.2 0.41 0.16 Siecino 729.7 mean 12.6 16 7.33 8 3.83 5.83 1.66 1.83 Wilczkowo 300 mean 14 16.1 7.33 7.8 3.7 8 0.92 0.33 Wielkopolskie Lakeland Karpicko 116 large 29 20 7.5 8.5 1 8.5 2 0.5 Konin 93.5 mean 20.5 18.5 7.25 8.75 3.5 11.6 1.25 0.62 Orchowe 163 large 18.7 19 7.3 8.16 3.3 9.36 2.5 0.75 Sławskie 817.3 large 18.5 18.66 7.25 8.33 5.4 7.2 0.5 0.5 Wilcze 48.2 little 16.6 19.16 6.5 8 2.5 7.8 1.5 0.16 Dam reservoirs Goczałkowice 3200 large 17.3 17.8 7 7.67 3.86 8.1 1.16 0.42 Kozłowa Góra 556 large 18 19 7.5 8.5 5 9 0.5 0.25 Łąka 418 mean 18.7 18.3 7.3 8.3 1.9 8.7 1.92 0.58 Paprocany 105 little 17 18 5.5 7.5 5.6 8.3 0.25 0.25 Drowned sand pit Dziećkowice 433 large 16.5 17.5 7.25 7.5 4.25 8.25 0.62 0 Dzierżno Duże 615 large 21 23 7.5 8.5 0.4 5 3.5 1.5 Pławniowice Duże 250 large 16 18 7.5 8.5 5.35 8.3 1.75 0.125Pogoria I 60 large 19.75 19.75 5.5 8 3.4 8.55 1.75 0 Pogoria III 208 large 19.5 18 6.5 7.75 4.05 8.6 0.125 0.125



10

Differences in evenness, species diversity H’, PIE and IFO indexes between

lakes and reservoirs were statistically not significant. However, mean values of species diversity H’, PIE for psammon rotifer communities in drowned sand pit were the lowest (Table 2).

Rotifer communities of drowned sand pit were characterised by high values of species number and lower index of faunal originality (IFO) in comparison with the ones in lakes and dam reservoirs (Table 2).

According to Morisity index (which designates similarity structure of dominant community only by taking into consideration the species of very high abundance), three classes of reservoirs were distinguished (Fig. 1). In the first class there were all lakes and one dam reservoir, Kozłowa Góra. In the second one there were reservoirs Paprocany, Pogoria III and lake Zbąszyńskie, the others artificial reservoirs were qualified to the third class. However, the values of Sörensen index did not show differences between communities of rotifers in tested reservoirs, so it was not possible to distinguish the above mentioned three classes.

Table 2

Number of species, total number of individuals, evenness E, indexes of species diversity H’ and PIE, index of faunal originality IFO of psammon rotifers in lakes and reservoirs

Lakes N. species Indiv. dm-3 E H' PIE IFO Jeleń 29 24 047 0.49 2.33 0.842 0.17 Sarcze 57 51 683 0.62 2.91 0.912 0.27 Siecino 51 58 841 0.62 2.92 0.917 0.22 Wilczkowo 43 76 167 0.49 2.36 0.843 0.17 Karpicko 14 1 422 0.37 1.76 0.733 0.08 Konin 26 10 177 0.17 1.97 0.757 0.13 Orchowe 35 17 047 0.58 2.72 0.908 0.14 Sławskie 39 96 641 0.42 2.01 0.804 0.22 Wilcze 41 12 000 0.5 2.37 0.829 0.22 Dam reservoirs

Goczałkowice 27 29 267 0.39 1.86 0.703 0.14 Kozłowa Góra 27 20 843 0.55 2.61 0.896 0.13 Łąka 13 12 178 0.43 2.03 0.835 0.23 Paprocany 37 55 244 0.57 2.69 0.889 0.21 Drowned sand pit

Dziećkowice 38 154 704 0.45 2.15 0.826 0.16 Dzierżno Duże 19 91 426 0.09 2.3 0.22 0.16 Pławniowice Duże 33 31 478 0.49 0.6 0.827 0.16 Pogoria I 20 30 592 0.42 1.96 0.817 0.18 PogoriaIII 27 44 078 0.36 1.71 0.606 0.13

Comparison of psammon rotifers community in lakes and artificial reservoirs

www.oandhs.org

11

CONCLUSION

Evenness index and species diversity index have shown that psammon communities of rotifers in natural lakes and artificial reservoirs are similar. Similarity of rotifer communities was better determined by Morisity index than by Sörensen index.

Faunal originality index was higher in the natural lakes than in the artificial reservoirs, except Łąka reservoir.

REFERENCES

Bielańska-Grajner I., 2001, The psammic rotifer structure in three Lobelian Polish lakes differing in pH, Hydrobiologia 446/447, 149-153.

Bielańska-Grajner I., 2004, Preliminary investigations of psammon rotifers in two reservoirs in Upper Silesia, Oceanol., And Hydrobiol. Studies, 33, 37-45.

Bielańska-Grajner I., 2005, Psammon rotifers (Rotifera) inhabiting water reservoirs in selected areas of Poland, 14 pp, English summary.

Ejsmont-Karabin J., 1995, Rotifer occurrence in relation to age, depth and trophic state of quarry lakes, Hydrobiologia, 131/314, 21-28.

UPGMA

Zmodyfikowany wskaźnik Morisity

JeleńWilczeKarpickoKoninOrchoweKozłowa GóraSarczeSiecinoWilczkowoSławskieZbąszyńskiePogoriaIIIPaprocanyGoczałkowicePławniowice DuDzierżno DużeDziećkowicePogoria IŁąka

0.04 0.2 0.36 0.52 0.68 0.84 1

Modified Morisita’s Similarity

Fig. 1. Modified Morisita's Similarity.



12

Ejsmont-Karabin J., 2003, Rotifera of lake psammon: community structure versus trophic state of lake waters, Pol. J. Ecol., 51, 5-35.

Horn H. S., 1966, Measurement of “overlap” in comparative ecological studies, Am. Nat., 100, 419-424.

Krebs J. C., 1989, Ecological Methodology, New York, 654 pp. Lampert W., Sommer U., 1996, Ecology of inland water, PWN, Warszawa, 389 pp. Radwan S., Bielańska-Grajner I., 1998, Preliminary investigations on the biotic structure of

psammic rotifers in the water bodies of Southern-Eastern Poland, Abstract of the VIIIth International Rotifer Symposium, Collegeville,1997.

Radwan S., Bielańska-Grajner I., 2001, Ecological structure of psammic rotifers in the ecotonal zone of Lake Piaseczno (eastern Poland), Hydrobiologia, 446/447, 221-228.

Wiszniewski J., 1934, Les Rotifères psammiques, Ann. Musei Zool. Pol.,10, 339-399. Wiszniewski J., 1947, Remarques relatives aux recherches recentes sur le psammon d’eaux

douces, Arch. Hydrobiol. i Ryb., 13, 7-36.




(13-19) 2007



Distribution of Oligochaeta in various littoral habitats in the anthropogenic reservoirs

Elżbieta Dumnicka1

Institute of Chemistry and Environmental Protection Jan Długosz University of Częstochowa

ul. Armii Krajowej 13/15, 42-200 Częstochowa, Poland

Key words: Częstochowa Upland, sediments, macrophytes, plastic rubbish, Naidinae, Lumbriculus variegates, Bothrioneurum veydovskyanum

Abstract

The study was carried out in the littoral of 2 clay-pits situated in Częstochowa city (Southern Poland). Samples of macroinvertebrates were collected from bottom sediments, submerged plants and plastic rubbish. The highest number of oligochaete species was found in benthos (20 species in pit no 1 and 16 in pit no 2) whereas the number of epiphitic species was distinctly smaller and similar on both substrates (9-10 in pit no 1 and 6 – 7 in pit no 2). Among oligochaetes, subfamily Tubificinae and Nais pardalis were more abundant on the bottom (P<0.01) whereas in periphyton, besides Naidinae, species regarded as typical for benthos (Lumbriculus variegatus and Bothrioneurum veydovskyanum) were more numerous (P<0.01 and P<0.05, respectively).



July 05, 2007 December 12, 2007

E. Dumnicka


14

INTRODUCTION

In Poland, detailed parallel studies concerning periphytic and benthic oligochaetes were performed sporadically and only in natural water bodies. Moszyński and Moszyńska (1957) presented the lists of oligochaete species living in various zones of the littoral, including macrophytes zones, and Kasprzak (1976) published quantitative data on oligochaetes found among macrophytes and mosses in a small lowland river. Also in other countries such studies were only occasionally performed (Verdonschot 2001, Mastrantuono and Mancinelli 2005). Oligochaetes living on plastic rubbish have been rarely studied yet (Czarnecka 2005) though such a study was done for other artificial substrata (Szlauer and Szlauer 1997, Czarnecka 2005).

In southern Poland, stagnant water bodies are mainly of anthropogenic origin and the detailed studies on some faunistic groups showed that taxocens living in such reservoirs could be interesting for the occurrence of species considered to be rare and the presence of quite rich fauna of oligochaetes (Dumnicka and Krodkiewska 2003), leeches (Krodkiewska 2003) and rotifers (Bielańska – Grajner 1983/1984).

The aim of the present study was to evaluate the composition and structure of oligochaete taxocens found at the same time in three studied littoral habitats: bottom, submerged macrophytes and plastic rubbish. Also an attempt was made to explain why typically benthic species (Lumbriculus variegatus and Bothrioneurum veydovskyanum) occurred numerously in the periphyton.

STUDY AREA AND METHODS

The studies were done in 2 small clay-pits flooded in 1960 and connected by a canal in 1970. The water chemistry in both pits is similar (Jatulewicz 2007) but the first reservoir has sandy landslip bank what affects its bottom character, while the second one has low and well consolidated bank (Table 1).

On each reservoir only one sampling site (Fig. 1) was studied from April 2005 to November 2005, mainly at 1-month intervals. Bottom fauna was collected quantitatively using a bottom scraper with 0.3 mm mesh net, while epiphitic fauna was collected only qualitatively from plastic rubbish (like PET bottles, plastic bags etc.) and from submerged plants and then washed on a cuvette. All samples were fixed with 4% formaldehyde and sorted under a stereoscopic microscope. Oligochaetes were identified to the species level using the keys of Brinkhurst and Jamieson (1971) and Kasprzak (1981, 1986), systematics of family Tubificidae was assumed after Erseus and Gustavsson (2002). Percentage share of each taxon in total number of oligochaetes and in particular studied habitats was calculated. The significance of differences in

Oligochaeta in the littoral of anthropogenic reservoirs

www.oandhs.org

15

taxocens structure was calculated using a non-parametric test (Mann-Whitney test) by STATISTICA 6.0 software package (STAT SOFT).

RESULTS

Taking into account all habitats of both studied water bodies, 24 species and 2 genera of oligochaetes were determined (Table 2). They belonged to 3 families: Tubificidae (with Naidinae, Rhyacodrilinae and Tubificinae subfamilies), Enchytraeidae and Lumbriculidae, but only Tubificinae and Naidinae were numerous and represented by many species. Somewhat higher number of species was stated in pit no 1 than in pit no 2, but only 12 species were found in both water bodies studied.

1

2

POLAND

N

Fig. 1. Location of Częstochowa city and locality of the sampling sites (dots) in studied reservoirs.

Table 1 Short characteristic of the studied pits and sites

Parameters Reservoir no 1 Reservoir no 2 Area (ha) 5.5 3.0 Depth of reservoir (m) 4.0 4.0 Depth of sampling point (m) 0.3 – 0.5 0.3 – 0.5

Plants at sampling point single tufts of

Ceratophyllum sp. and Myriophyllum sp.

single tufts of Ceratophyllum sp. and Myriophyllum sp.;

emergent plants also present Character of the bottom in littoral sand and mud mud and detritus

E. Dumnicka


16

In contrast to the results obtained for the whole fauna, the highest number

of oligochaete species was found in benthos (20 species in pit no 1 and 16 in pit no 2) whereas the number of periphytic species was distinctly smaller and similar on both substrates: 9 – 10 species found on plants and plastic rubbish in the reservoir no 1, and 6 - 7 species in analogous habitats in the reservoir no 2 (Table 2). Although the highest number of species was found on the bottom, the highest values of Shannon-Weaver index were stated for oligochaetes found among plants (Table 2) due to more even abundance of prevailing species.

In studied reservoirs there were species abundantly or exclusively found on the bottom and rarely on two other substrata, like all species from the subfamily Tubificinae, including juvenile specimens. On the sandy bottom of pit no 1 Naidinae were also abundant and diversified, for example the abundance of

Table 2 Percentage contribution of Oligochaeta species in the studied habitats and in both reservoirs (total)

Reservoir no 1 Reservoir no 2 bottom plants rubbish total bottom plants rubbish total OLIGOCHAETA Ophidonais serpentina (O.F. Műll.) 4.3 19.2 40.9 9.9 10.6 16.7 20.3 12.9 Dero spp. Oken 1.8 1.3 3.0 2.3 5.1 3.6 Stylaria lacustris (L.) 0.6 3.8 0.9 2.1 6.9 19.0 5.4 Nais christinae Kasprzak 2.6 11.5 4.5 3.9 0.3 18.1 12.7 4.9 Nais pardalis Piguet 17.0 1.3 13.2 0.5 0.4 Nais barbata O.F. Műll. 3.0 15.4 15.2 5.7 0.8 5.1 5.1 1.7 Nais communis Piguet 0.4 0.3 Nais variabilis Piguet 3.8 9.1 1.4 1.4 0.2 Nais pseudobtusa Piguet 0.2 0.2 Nais spp. O.F. Műll. 1.5 0.2 Vejdovskyella intermedia (Brets.) 1.0 0.8 Slavina appendiculata (d’Udekem) 0.4 14.1 4.5 2.6 1.9 2.8 1.3 1.9 Chaetogaster diastrophus (Gruit.) 0.2 0.2 Pristina rosea (Piguet) 0.2 0.2 Pristina foreli (Piguet) 1.4 0.2 Tubificinae gen. spp. juv. 59.6 12.5 4.5 47.6 60.4 6.9 1.3 44.3 Limnodrilus hoffmeisteri Clap. 6.3 1.5 5.0 6.6 1.4 4.9 Limnodrilus claparedeanus Ratzel 0.2 0.3 0.3 2.1 1.5 Limnodrilus profundicola (Verrill) 0.2 0.2 Limnodrilus udekemianus Clap. 4.8 3.4 Tubifex tubifex (O.F. Műll.) 0.3 0.2 Tubifex ignotus (Štolc) 0.5 0.4 Aulodrilus pluriseta (Piguet) 1.0 0.8 0.5 0.4 Bothrioneurum vejdovskyanum Štolc 0.2 2.6 4.5 0.9 2.4 8.3 2.8 Marionina riparia Bretscher 0.2 0.2 Marionina argentea (Michaelsen) 0.2 0.2 Cognettia spp. juv. Niel. et Christ. 0.3 0.2 Lumbriculus variegatus (O.F. Műll.) 0.2 14.1 10.6 3.0 0.8 33.4 40.5 10.7 Shannon-Weaver index 2.13 3.13 2.74 2.77 2.24 2.78 2.20 2.84


www.oandhs.org

17

Nais pardalis was distinctly higher in benthic (Table 2) than in periphytic samples (P<0.01). On the muddy bottom in pit no 2 Tubificinae such as Limnodrilus udekemianus and Tubifex tubifex typical for sediments of this kind occurred. A few taxa representing family Enchytraeidae were also found on the bottom. The majority of species from subfamily Naidinae was more abundant in periphyton, among them the most numerous were Ophidonais serpentina and species representing genus Nais: N. christinae and N. barbata. Among plants as well as on plastic rubbish Lumbriculus variegatus (Lumbriculidae) and Bothrioneurum veydovskyanum (Rhyacodrilinae, Tubificidae) were more numerous than in benthic samples and these differences were statistically significant (P<0.01 and P<0.05, respectively).

DISCUSSION

The number of oligochaete taxa found in the studied habitats of two clay pits was similar to that stated by Mastrantuono and Mancinelli (2005) in analogous habitats of a natural lake but smaller than stated by Moszyński and Moszyńska (1957) in Mazurian lakes. In other anthropogenic reservoirs the diversity of oligochaete fauna was usually smaller – the number of determined taxa did not exceed 15 (Czarnecka 2005, Dumnicka and Krodkiewska 2003, Dumnicka and Galas 2006) but could be extremely low, e.g. 3 taxa in benthos of coal strip mine ponds (Canton and Ward 1981). The composition and structure of benthic oligochaete taxocens living in the studied reservoirs were typical for soft bottom but epiphytic taxocens differed from these stated in other water bodies.

In periphyton the domination of naidids, (represented mainly by Stylaria lacustris) was stated in some studies concerning the whole fauna of this habitat (Soszka 1975, Kornijów 1989). Detailed studies on periphytic oligochaetes living on plants showed that in this habitat beside Stylaria, other naidids such as genus Pristina, some representatives of genera Chaetogaster and Nais were numerous (Kasprzak 1976, 1985; Kuflikowski 1986; Mastrantuono and Mancinelli 2005). Species belonging to the last mentioned genera are small and may be lost, especially from samples taken using apparatus with 0.5 mm mesh size net and sorted by a “naked eye”. In such a situation the percentage share of oligochaetes in the whole epiphytic fauna could be underscored, and at the same time the share of the largest species (Stylaria, Chaetogaster diaphanus) could be overstated.

Beside naidids, Lumbriculus variegatus and Bothrioneurum vejdovskyanum were found abundantly among plants and on plastic rubbish. According to the literature, L. variegatus is an ubiquitous species living on the bottom covered by decaying plants, near the shore of stagnant and running waters (Kasprzak 1981)

E. Dumnicka


18

but it could be abundant on artificial substrata also (Jeffries 1993). During summer L. variegatus feeds almost exclusively on algae (Moore 1978) that is why it could be a periphytic species. According to the published data, Bothrioneurum vejdovskyanum prefers the bottom of stagnant waters rich in organic matter (Kasprzak 1981, Hrabě 1981) but it could cluster on plastic rubbish also (Czarnecka 2005). Both these species reproduce mainly asexually - this feature is also characteristic for other species (belonging to the subfamily Naidinae) living among plants. Data from the studied pits (Jatulewicz in press) as well as those from the literature (Kasprzak 1985) show that predator pressure is higher among submerged plants than on the bottom. In such a situation asexual reproduction and fast regeneration of body parts facilitate survival of epiphytic species. Another favourable feature, which enables fast escape from predators, is the ability to swim, known in the majority of periphytic naidins and L. variegatus (Drewes 1999). Therefore, the division into periphytic and benthic species does not run in accordance with systematics, e.g. Naidinae –periphytic forms, the remaining families - benthic forms but rather follows ecological adaptations and requirements of particular species.

REFERENCES

Bielańska – Grajner I., 1983/1984, Rotifers (Rotatoria) of Lake Paprocańskie (Upper Silesia, Poland), Acta Hydrobiol., 25/26, 67-79.

Brinkhurst R. O., Jamieson B. G. M., 1971, Aquatic Oligochaeta of the world, Oliver & Boyd, Edinburgh, 860 pp.

Canton S., Ward J., 1981, Benthos and zooplankton of coal strip mine ponds in the mountains of northwestern Colorado, U.S.A., Hydrobiologia 85, 23 – 31.

Czarnecka M., 2005, Ekologiczny status epifauny zasiedlającej sztuczne podłoża podwodne. [Ecological status of epifauna settled on artificial submerged substrata], PhD thesis, Nicolaus Copernicus University, Toruń.

Drewes C. D., 1999, Helical swimming and body reversal behaviors in Lumbriculus variegatus (Annelida: Clitellata: Lumbriculidae), Hydrobiologia, 406, 263-269.

Dumnicka E., Galas J., 2006, Distribution of benthic fauna in relation to environmental conditions in an inundated opencast sulphur mine (Piaseczno reservoir, Southern Poland), Aquat. Ecol., 40, 203 – 210.

Dumnicka E., Krodkiewska M., 2003, Studies on freshwater Oligochaeta in the Upper Silesia region (Southern Poland), Biologia, Bratislava, 58, 897 – 902.

Erséus C., Gustavsson L., 2002, A proposal to regard the former family Naididae as a subfamily within Tubificidae (Annelida, Clitellata), Hydrobiologia, 485, 253 – 256.

Hrabě S., 1981, Vodni maloštetinatci (Oligochaeta) Československa [Aquatic oligochaetes (Oligochaeta) of Czechoslovakia], Acta Univ. Carolinae – Biologica, 1979, 1- 167.

Jatulewicz I., 2007, Comparison of macroinvertebrate communities associated with various habitats in anthropogenic reservoirs, Oceanol. Hydrobiol. Stud., 36 (Suppl. 4): 39-47

Jeffries M., 1993, Invertebrate colonization of artificial pondweeds of differing fractal dimension, Oikos, 67, 142 – 148.


www.oandhs.org

19

Kasprzak K., 1976, Badania nad skąposzczetami (Oligochaeta) dolnego biegu rzeki Wełny [Investigations of Oligochaeta of the lower part of Wełna River (Poland)], Fragm. Faun., 20, 425- 467. (in Polish with English summary).

Kasprzak K., 1981, Skąposzczety wodne, I. Rodziny: Aeolosomatidae, Potamodrilidae, Naididae, Tubificidae, Dorydrilidae, Lumbriculidae, Haplotaxidae, Glossoscolecidae, Branchiobdellidae. [Aquatic oligochaetes], Klucze do oznaczania bezkręgowców Polski, 4, Państwowe Wydawnictwo Naukowe, 226 pp. (in Polish).

Kasprzak K., 1985, Density, biomass, and respiration of phytophilous macrofauna of associations of Potamogeton perfoliatus L. of a polymictic, eutrophic lake, Acta hydrobiol., 27, 63-73.

Kasprzak K., 1986, Skąposzczety wodne i glebowe, II. Rodzina: wazonkowce (Enchytraeidae) [Aquatic and soil oligochaetes, II. Family: enchytraeids (Enchytraeidae)], Klucze do oznaczania bezkręgowców Polski, 5, PWN, 366 pp. (in Polish).

Kornijów R., 1989, Seasonal changes in the macrofauna living on submerged plants in two lakes of different trophy, Arch. Hydrobiol., 117, 49 – 60.

Krodkiewska M., 2003, Leech (Hirudinea) communities of post-exploitation water bodies in industrial region (Upper Silesia, Poland), Pol. J. Ecol., 51, 101 – 108.

Kuflikowski T., 1986, Development and structure of the Goczałkowice Reservoir ecosystem. XIII. Plant-dwelling fauna, Ekol. pol., 34, 473 - 489.

Mastrantuono L., Mancinelli T., 2005, Littoral invertebrates associated with aquatic plants and bioassessment of ecological status in Lake Bracciano (Central Italy), J. Limnol., 64, 43 -53.

Moore J. W., 1978, Importance of algae in the diet of the oligochaetes Lumbriculus variegatus (Műller) and Rhyacodrilus sodalis (Eisen), Oecologia, 35, 357 – 363.

Moszyński A., Moszyńska M., 1957, Skąposzczety (Oligochaeta) Polski i niektórych krajów sąsiednich [Oligochaetes of Poland and some neighbouring countries], Pozn. Tow. Przyjaciół Nauk, Wydz. Mat.-przyr., 18, 204 pp. (in Polish).

Soszka G. J., 1975, The invertebrates on submerged macrophytes in three Masurian lakes, Ekol. Pol., 23, 371 – 391.

Szlauer B., Szlauer L., 1997, Organisms colonizing polythene sheets deployed in Lake Miedwie (northwestern Poland, Acta Hydrobiol., 39, 111 – 119.

Verdonschot P. F. M., 2001, Hydrology and substrates: determinants of oligochaete distribution in lowland streams (The Netherlands), Hydrobiologia, 463, 249 – 262.




(21-28) 2007



Large branchiopods (Anostraca, Notostraca, Spinicaudata, Laevicaudata) of small, astatic waterbodies in the environs

of Poznań (Wielkopolska Region, Western Poland)

Bartłomiej Gołdyn1,*, Szymon Konwerski2, Jerzy Błoszyk1,2

1Department of General Zoology, Adam Mickiewicz University Ul. Umultowska 89, 61-614 Poznań, Poland

2Natural History Collections, Adam Mickiewicz University, Poznań, Poland Key words: fairy shrimp, clam shrimp, tadpole shrimp, Conchostraca, vernal pool, kettle hole

Abstract

We report new localities (67 ponds on three study areas) of six large branchiopod species: Branchipus schaefferi, Siphonophanes grubei, Triops cancriformis, Lepidurus apus, Lynceus brachyurus and Cyzicus tetracerus from small, astatic waterbodies in the Wielkopolska Region (Western Poland). Some notes on the species phenology and habitat preferences are also provided. The most remarkable species appears to be B. schaefferi, endangered in many countries of Europe, last recorded in Poland in 1956 and hitherto not reported from the western part of the country. We also express a need for more detailed studies and protection activities for maintaining the large branchiopod biodiversity and survival.

* Corresponding author: [email protected]


July 05, 2007 November 07, 2007

B. Gołdyn, S. Konwerski, J. Błoszyk


22

INTRODUCTION

Large branchiopods (Anostraca, Notostraca, Spinicaudata and Laevicaudata) are considered to be threatened worldwide (e.g. Hamer, Brendonck 1997; Weeks, Marcus 1997; Williams 2006) and their situation, due to decline of their natural habitats, seems to be especially critical in Europe (Eder et al. 1997; Biggs et al. 2004; Engelmann, Hahn 2004). They used to be common inhabitants of small, impermanent bodies of water like kettle hole ponds, vernal pools or large puddles, now disappearing from agricultural landscape due to intensified land melioration and changes in land use, enhanced by climate warming (Pyke 2005). Furthermore, excessive use of pesticides, insecticides and fertilisers in the agricultural catchments of waterbodies is an important factor responsible for decrease of large branchiopod populations in many countries of Europe.

In Poland the status of this group is uncertain, mainly due to the lack of recent studies concerning biology and distribution of large branchiopods in the country. Since quite wide popularity in the 1950's and 60's (e.g. Zwolski 1956; Hempel 1963; Mielewczyk 1957, 1963; Hajduk 1967) we had only a few papers reporting new Polish localities of large branchiopods (Biggs et al. 2004) or dealing with their physiology and biochemistry (e.g. Czeczuga, Czeczuga – Semeniuk 1998).

In this paper we report new localities of six large branchiopod species in the Wielkopolska Region: Anostraca: Branchipus schaefferi Fischer, 1834 and Siphonophanes grubei (Dybowski, 1860), Notostraca: Triops cancriformis (Bosc., 1801) and Lepidurus apus (L., 1758), Laevicaudata: Lynceus brachyurus Müller, 1776 and Spinicaudata: Cyzicus tetracerus (Krynicki, 1830). We also give some notes on the ecological preferences and phenology of those species.


Data on large branchiopod occurrence were collected in March – October 2002 – 2007 during studies on Coleoptera of Biedrusko range (e.g. Konwerski, Sienkiewicz 2005) and on malacocenoses of kettle hole ponds of Western Wielkopolska (see Gołdyn 2005 for the detailed characteristics of the ponds geomorphology and physico-chemical parameters of water and sediments). In total, 73 waterbodies were inspected, 53 of them at least 4 times a year. To determine the hydroperiod, the waterbodies were inspected once a month in 2002 and/or 2003. Semi-quantitative samples were collected with a 20 × 30 cm net, towed along the bottom for 0.5 m (area of one sample: ca. 0.2 × 0.5 = 0.1 m2). Each time 5 samples were collected from each microhabitat (vegetation

Large branchiopods in the environs of Poznań

www.oandhs.org

23

type) present on the area of the waterbody. Collected specimens are deposited in Natural History Collections, Faculty of Biology, Adam Mickiewicz University, Poznań.

RESULTS

Branchipus schaefferi was recorded in 32 puddles along a tank road on Biedrusko range (52°30'20'' N; 16°55'50'' E). The pools are located in natural depressions of ground moraine, intensively modified by driving of military vehicles. They are small (maximum surface area = 25 – 300 m2) and shallow (maximum depth = 40 – 80 cm). Most of the puddles are devoid of higher vegetation, 8 pools are partially covered with patches of Agrostis stolonifera, Alisma plantago-aquatica and Juncus articulatus. The waterbodies differ in hydroperiod: from puddles inundated for 1 – 2 months after snow melting and occasionally after heavy rain falls (n = 10), to permanent ones (n = 6). The sediments are loamy and sandy in all the puddles and water is often turbid.

In all the pools B. schaefferi occurred since April until October, if they did not dry off before. The populations were most abundant in June, reaching densities up to 120 individuals m-2. The sex ratio was always nearing 1 : 1 (Male : Female). The populations seem to be stable; they were observed in all the years of the study (2003 – 2006).

Siphonophanes grubei was found in 27 among 34 kettle hole ponds studied in agricultural landscape of the environs of Tarnowo Podgórne (52°29'14'' N; 16°36'50'' E) and in 7 forest potholes in the Rogoźno district (52°40'16'' N; 16°59'57'' E) (Table 1). The ponds differed a lot with respect to maximum area (100 – 1500 m2), depth (30 – 150 cm), hydroperiod (from highly ephemeric, drying out for 9 months a year to permanent ones) and vegetation structure. In all of the kettle holes located in agricultural landscape sediments were sandy with low organic matter content (mean = 17.8%), whereas bottom of forest potholes was always covered with thick layer of leaves (mainly of Alnus glutinosa and Fagus silvatica).

S. grubei occurred since late March until the beginning of May in the years 2002 – 2004 and 2007. Its abundance varied from 4 ind. m-2 (permanent ponds with submerged vegetation) to 50 ind. m-2 (ephemeric ponds, amphibiotic vegetation). The sex ratio was also variant, from 1 : 1 to 1 : 4 (M : F). The species was absent only in five permanent kettle hole ponds where fish (Carassius sp.) occurred and in two waterbodies completely covered by reed (Phragmites australis).

Lepidurus apus was found in 7 of the above-mentioned kettle holes near Tarnowo Podgórne, simultaneously with S. grubei. The ponds differed in their hydroperiod (drying for 2 – 10 months a year) and amphibiotic vegetation cover



24

Table 1

Localities of four large branchiopod species in sampled ponds of agricultural and forrest (a) landscape with the data on the waterbodies hydroperiod and amphibiotic vegetation cover. Six permanent ponds located in the environs of Tarnowo Podgórne where we did not find any species from the group are not presented

Latitude (N)

Longitude(E) S. grubei L. apus C. tetracerus L. brachyurus Hydroperiod

(months)

Vegetation cover (%)

52º28'14'' 16º32'13'' + 12 90 52º28'16'' 16º37'53'' + 12 50 52º29'24'' 16º36'06'' + 11 25 52º29'26'' 16º32'44'' + 11 70 52º29'38'' 16º32'57'' + 10 95 52º28'16'' 16º31'53'' + 10 75 52º29'25'' 16º36'19'' + + 10 80 52º29'39'' 16º32'59'' + + 10 95 52º29'32'' 16º36'23'' + + + + 9 35 52º28'57'' 16º37'32'' + 9 85 52º28'01'' 16º37'50'' + + + 9 20 52º28'23'' 16º37'49'' + 9 10 52º28'02'' 16º37'52'' + + + 9 40 52º29'05'' 16º36'41'' + + + 8 25 52º40'13'' 17º00'04'' + 8 0a

52º28'48'' 16º37'09'' + + 7 15 52º28'54'' 16º37'09'' + 7 30 52º28'43'' 16º37'08'' + 7 65 52º29'33'' 16º36'26'' + + 7 85 52º29'02'' 16º37'08'' + + + 6 10 52º28'28'' 16º37'12'' + + + 6 0 52º29'05'' 16º37'09'' + + + + 6 10 52º28'53'' 16º36'31'' + + 6 15 52º28'17'' 16º31'48'' + 6 10 52º28'30'' 16º32'04'' + 6 80 52º28'40'' 16º30'35'' + 6 60 52º40'11'' 17º00'09'' + 6 15a

52º28'50'' 16º37'09'' + + + 5 15 52º40'08'' 17º00'37'' + 5 0a

52º40'07'' 17º00'22'' + 5 0a

52º28'33'' 16º37'10'' + 5 100 52º40'09'' 17º00'11'' + 4 10a

52º40'31'' 16º59'49'' + 4 0a

52º40'10'' 17º00'13'' + 4 0a

52º28'35'' 16º37'34'' + + 3 70


www.oandhs.org

25

(Tab. 1). During our samplings the abundance of L. apus did not exceed 1 specimen m-2. All of about 30 individuals collected were females.

Triops cancriformis was recorded in 19 pools on the Biedrusko Military Area (see above). All the waterbodies were temporary (drying out at least for 3 months a year). T. cancriformis occurred from April until late September. Its abundance was always below 4 ind. m-2, and only females were recorded (n = 34). In June 2003 we observed predation of T. cancriformis on B. schaefferi.

Lynceus brachyurus occurred in late May – June of 2002 and 2003 in 11 ponds in the environs of Tarnowo Podgórne. The populations were very abundant, reaching 700 ind. m-2 (mean = 185.4). The ponds where L. brachyurus was found had significantly lower water conductivity than the other ponds studied (mean = 324 μS cm-1 against the mean of 496 μS cm-1 for the 34 studied waterbodies of Tarnowo Podgórne; One-way ANOVA: F = 4.658; p = 0.041).

Cyzicus tetracerus occurred in May – June of 2002 and 2003 in 7 of the kettle holes near Tarnowo Podgórne. Its abundance was considerably smaller than that of L. brachyurus (max 8 ind. m-2, mean 2.8), no males were found. All the ponds where C. tetracerus occurred, desiccate for 3 – 7 months a year and have scarce vegetation cover. Furthermore, all but one pond are surrounded by trees or bushes (Populus sp. or Salix sp.) with their leaves covering the bottom.

DISCUSSION

Among the large branchiopod species found in the environs of Poznań, B. schaefferi seems to be the rarest and most endangered. Although in the past it was believed to be quite common in the country (e.g. Wierzejski 1896, Momot 1913), until now there were only five known localities in Poland, all of them described at least 50 years ago. Furthermore, there were no reports of this species from the western part of the country (the environs of Kraków: Wierzejski 1896; Warsaw: Sumiński, Tenenbaum 1921; Kraków: Ramułt 1939; the vicinities of Lublin and Sandomierz: Zwolski 1956). Although the species has a wide, Western – Palearctic and partially Oriental distribution (Brtek, Thiéry 1995; Petkovski 1997), in many countries it is regarded as endangered. In Austria, where 34 localities were recorded, B. schaefferi alike other large branchiopods is planned to be included into the “National Red List of Animals” (Eder et al. 1997, Engelmann, Hahn 2004). In Germany, where 48 localities are known (at least 16 of them nowadays historical), it was classified as highly endangered and has been strictly protected since 1987 (Maier 1998, Engelmann, Hahn 2004).

Although the populations of B. schaefferi found on the Biedrusko Military Area are abundant and stable, they seem to be restricted to the area of some



26

4 km2 and this species was not found to occur outside the range. Such a situation appears to be typical for the species – in Germany present distribution of B. schaefferi is believed to be limited to the military areas, probably due to the changes in land use in agricultural landscape, where it used to occur in the past (Maier 1998). Similar situation is observed also in Austria and Czech Republic, where localities of B. schaefferi from military training grounds are known.

Despite the scarcity of recent published data, other large branchiopod species considered in the present paper seem to be quite common in Poland. For instance, Zwolski (1956) cites 8 localities of S. grubei, 11 of L. brachyurus and 5 of C. tetracerus, all from different parts of the country. L. apus and T. cancriformis are, according to the above-mentioned author, common in the area of Poland. Brtek and Thiéry (1995) give similar number of localities, probably based on the same literature, although regarding to Notostraca species they bring up only 3 and 6 localities, respectively. Recent paper of Biggs et al. (2004) reports occurrence of S. grubei, L. apus and C. tetracerus in 32% of 200 ponds studied in the surroundings of Białystok (E Poland).

Last records of S. grubei, L. apus, L. brachyurus and C. tetracerus from the Wielkopolska Region come from two midfield ponds and one puddle in the environs of Gniezno (approximately 60 km east from the localities described in the present paper; Mielewczyk 1957, 1963). S. grubei, L. apus and T. cancriformis were also reported by Szafran (1959) from a floodplain in the area of the city of Poznań.

Similarly to the conclusions drawn by Biggs et al. (2004) and contrary to the situation observed in other countries of Europe (e.g. Damgaard, Olesen 1998, Eder et al. 1997, Maier 1998) large branchiopod fauna of western Poland seems to be relatively unaffected by human activity. All the more, it requires detailed studies and protection regulations and activities (e.g. Rogers 1998; Kalettka et al. 2001) to maintain the status quo and prevent the threats caused by decline of habitats and extensive agriculture. It is especially substantial for B. schaefferi whose situation could be already similar to that observed in Germany.

ACKNOWLEDGEMENTS

The research described here has been supported by the Polish Ministry of Science and Higher Education grant no. N N304 3400 33.

REFERENCES

Biggs J., Bilton D., Williams P., Nicolet P., Briggs L., Eeles B., Whitfield M., 2004, Temporary ponds of eastern Poland: an initial assessment of their importance for nature conservation,


www.oandhs.org

27

Arch. Sci., 57: 73-84 Brtek J., Thiéry A., 1995, The geographic distribution of the European Branchiopods (Anostraca,

Notostraca, Spinicaudata, Laevicaudata), Hydrobiologia, 298: 263-80 Czeczuga B., Czeczuga-Semeniuk E., 1998, Carotenoprotein complexes in Chirocephalus

diaphanus Prévost, Fol. Biol. Krak., 46(3-4): 197-201 Damgaard J., Olesen J., 1998, Distribution, phenology and status for the larger Branchiopoda in

Denmark, Hydrobiologia, 377: 9-13 Eder E., Hödl W., Gottwald R., 1997, Distribution and phenology of large branchiopods in

Austria, Hydrobiologia, 359: 13-22 Engelmann M., Hahn T., 2004, Vorkommen von Lepidurus apus, Triops cancriformis,

Eubranchipus (Siphonophanes) grubii, Tanymastix stagnalis und Branchipus schaefferi in Deutschland und Österreich (Crustacea: Notostraca und Anostraca). Faun. Abh. 25: 3–67

Gołdyn B., 2005, Influence of selected environmental factors on malacocenoses of midfield kettle holes, PhD thesis, Adam Mickiewicz Univ., Poznań, pp 144, (in Polish)

Hajduk Z., 1967, Further report on Limnadia lenticularis (L.) (Euphyllopoda-Crustacea) in Silesia, Opol. Tow. Przyj. Nauk., Zeszyty Przyrodnicze, 7: 101-4

Hamer M.L., Brendonck L., 1997, Distribution, diversity and conservation of Anostraca (Crustacea: Branchiopoda) in southern Africa, Hydrobiologia 359: 1–12

Hempel J., 1963, Biological observations dealing with Triops cancriformis (Bosc) under natural and laboratory breeding conditions, Ann. Zool., 20: 343-52, (in Polish with Engl. summ.)

Kalettka T., Rudat C., Quast J., 2001, “Potholes” in Northeast German agro-landscapes: functions, land use impacts, and protection strategies, Ecol. Stud., 147: 291-8

Konwerski Sz., Sienkiewicz P., 2005, Leiodidae (Coleoptera) of the Biedrusko range in Western Poland, [in:] Protection of Coleoptera in the Baltic Sea Region, Eds Skłodowski J., Huruk S., Barševskis A., Tarasiuk S., Warsaw Agricultural University Press, 129-36

Maier G., 1998, The status of large branchiopods (Anostraca; Notostraca, Conchostraca) in Germany, Limnologica, 28: 223-8

Mielewczyk S., 1957, A new locality of Limnadia lenticularis L. (Crustacea, Euphyllopoda), Przyr. Pol. Zach., 1 (1-2): 155-7, (in Polish with Engl. summ.)

Mielewczyk S., 1963, Two interesting species of Euphyllopoda: Cyzicus tetracerus (Kryn.) and Lynceus brachyurus O.F. Müll. near Gniezno, Przyr. Pol. Zach., 7 (1-4): 95-8, (in Polish with Engl. summ.)

Momot J., 1913, Entomostraca of Podolan craters, Wyd. Dankiewicz, Stanisławów, pp 68, (in Polish)

Petkovski S., 1997, On the presence of the genus Branchipus schaefferi, 1766 (Crustacea: Anostraca) in Macedonia, Hydrobiologia, 359: 37–44

Pyke C.R., 2005, Assessing climate change impacts on vernal pool ecosystems and endemic branchiopods, Ecosystems, 8(1): 95-105

Ramułt M., 1939, Euphyllopoda in the environs of Kraków, Spraw. Kom. Fizjograf. PAU, 73: 261-74, (in Polish)

Rogers D.C., 1998, Aquatic macroinvertebrate occurrences and population trends in constructed and natural vernal pools in Folsom, California. [in]: Ecology, conservation, and management of vernal pool ecosystems − proceedings from a 1996 Conference, Eds. Witham C.W., Bauder E.T., Belk D., Ferrin W.R.Jr., Orduff R. California Native Plant Society, Sacramento, CA., 224-35

Sumiński S.M., Tenenbaum Sz., 1921, Zoological guide to the surroundings of Warsaw, Wyd. M. Arct, Warszawa, pp 58, (in Polish)

Szafran H., 1959, City of Poznań and its surroundings, Pozn. Tow. Przyj. Nauk, Poznań, pp 383, (in Polish)

Weeks S.C., Marcus V., 1997, A survey of the branchiopod crustaceans of Ohio, Ohio J. Sci.



28

97(4): 86-9 Wierzejski A., 1896, A review of the galician Crustacea, Spr. Kom. Fizyogr. Akad. Um., Kraków,

31: 160-215, (in Polish) Williams D.D., 2006, The biology of temporary waters, Oxford Univ. Press, 337 pp. Zwolski W., 1956: Materials to the knowledge of the Polish Euphyllopoda, Ann. Univ. M. Curie-

Skłodowska, Sec. C, Lublin, 11: 1-23, (in Polish with Engl. summ.)




(29-37) 2007



Macroinvertebrate benthic communities in the macrophyte-dominated Lake Łuknajno (northeastern Poland)

Izabela Jabłońska–Barna1

Chair of Applied Ecology, Faculty of Environment Sciences and Fisheries University of Warmia and Mazury

ul. Oczapowskiego 5, 10-957 Olsztyn, Poland Key words: macroinvertebrates, shallow lake, Lake Łuknajno

Abstract

The analysis of the macroinvertebrates of the shallow, macrophyte-dominated Lake Łuknajno (north-eastern Poland) was performed. The studies covered the areas of the bottom overgrown by plants as well as denuded of macrophytes. Within benthic macrofauna, the representatives of 6 phyla typical of shallow, mesotrophic lakes were recorded. The relationship between the occurrence of particular taxa and the kind of plant cover was found only in the case of some molluscs and Camptochironomus tentans larvae.

The mean number and biomass of benthic fauna achieved 1135 individuals and 8.876 grams of wet weight per square meter, respectively. The dynamics of the community number was conditioned by temporal and spatial diversification of Chironomidae and Ephemeroptera larvae abundance. Bivalvia were the main component of the benthofauna biomass. 1 e-mail: [email protected]


July 05, 2007 November 07, 2007

I. Jabłońska-Barna


30

INTRODUCTION

The studies of benthofauna usually focus on the mid-lake zone. Little attention has been paid to the littoral zone where macroinvertebrates can occupy both water plants and bottom. Lake Łuknajno is a perfect place for such studies due to the fact that it is covered by dense macrophyte beds. There is lack of data on the benthic zoocenosis of the lake. Hitherto performed studies concerned hydrochemical condition of lake waters (Kufel & Ozimek 1994, Kufel & Kufel 1997, Ejsmont-Karabin et al. 1996), macrophyte structure (Królikowska 1997) and zooplankton (Karabin et al. 1997, Bowszys et al. 2006, Muirhead et al. 2006).

The aim of the present study was to estimate taxonomic structure, the number and biomass of the macrozoobenthos community inhabiting the bottom of the macrophyte-dominated Lake Łuknajno.


Lake Łuknajno is situated in the Great Masurian Lakes Region (53°49’N, 21°38’E) in the northeastern part of Poland. Due to its natural values, in particular diversified and abundant ornithofauna, the lake has been protected as a Nature Reserve since 1937 and Biosphere Reserve since 1977. It is a relatively small (623 ha), shallow (mean depth – 0.6 m; maximum – 3.0 m), eutrophic lake. The submerged macrophytes cover about 50% of the lake bottom.

The studies of macroinvertebrates were carried out in the years 2004-2006 as a part of complex studies of the lake that included the analyses of physico-chemical properties of lake water, characteristics of fish, phyto- and zooplankton communities. The present paper presents only the results of the studies on benthic invertebrates.

The material was collected monthly from May to November at four sampling stations (Figure 1): station No 1 – located within the emergent plant belt, dominated by Phragmites australis (Cav.) Trin. and Thypha angustifolia L.; station No 2 – located within the bottom overgrown by submerged vegetation patches - Chara sp.; station No 3 – the bottom denuded of macrophytes, with single individuals of Najas sp.; station No 4 – the bottom covered by Stratiotes aloides L.

Benthos samples were taken using the Kajak tube sampler with working area of 40.7 cm2 and sieved through a 0.25 mm mesh. Each sample taken from particular site was composed of 5 subsamples.

The biomass was estimated partially based on fresh weight of particular taxonomic groups in the samples, with accuracy of 0.1 mg.

Macroinvertebrate benthic communities in macrophyte-dominated lake

www.oandhs.org

31

Chironomidae larvae from genus Chironomus were identified using

cytogenetic methods (Jabłońska-Barna & Michailova in press).

RESULTS

The occurrence of 6 invertebrates phyla: Oligochaeta, Hirudinea, Insecta (Ephemeroptera, Odonata, Trichoptera and Diptera), Gastropoda, Bivalvia and Malacostraca (Isopoda) was recorded.

The mean number and biomass of benthic fauna achieved 1135 indiv. m-2 and 8.876 g m-2, respectively – Table 1.

Insects were the most diversified taxonomically and the most abundant phylum in Lake Łuknajno (Table 1, 2) constituting 88% of the total number of benthic animals inhabiting the bottom of the lake. The highest biomass achieved Bivalvia – 58% of the total community mass.

Within zoocenosis of the bottom of Lake Łuknajno, the distinct seasonal variations of the total number with clear summer minimum were recorded (Figure 2). The latter reflected life cycle of insects (the dominating benthos group) that undergo pupal metamorphosis in summer before leaving water environment. High overall benthos number was recorded in spring and in autumn.

Fig. 1. Location of the sampling sites in Lake Łuknajno; 1-4 – site numbers.



32

Table 1

Density (L - ind. m-2) and biomass (B - g m-2) of macrobenthic comunity in Lake Łuknajno - the mean values (2004-2006)

Taxon L B OLIGOCHAETA 61 0.2884HIRUDINEA 9 0.2097MALACOSTRACA 60 0.5253INSECTA

Ephemeroptera 208 0.1997Odonata 6 0.1104Trichoptera 28 0.1601Diptera Ceratopogonidae 14 0.0732 Chironomidae 734 1.7540 Chaoboridae 2 0.0058Megaloptera 2 0.1124Coleoptera 1 0.0163

GASTROPODA 3 0.2603BIVALVIA 6 5.1577Total 1135 8.8760

Fig. 2. Sesonal variations of bethic macroinvertebrate number (year 2005).


www.oandhs.org

33

The community biomass did not show similar seasonal fluctuations due to

the fact that its general magnitude depended on the contribution of Bivalvia. The observed variations in biomass were usually the effect of accidental sampling of some large individuals of that phylum (Figure 3, 4).

Table 2

Composition of Insecta comunity at different sampling sites (2004-2006) Taxon Station number 1 2 3 4INSECTA Ephemeroptera Amelytus inopinatus (Linnaeus) + +Caenis horaria (Linnaeus) + + + +Odonata Ischnura elegance (Vander Linden) + Enallagma cyathigerum (Charpentier) + Trichoptera Cyrnus crenaticornis (Kolenati) + + +Cyrnus flavidus McLachlan +Cyrnus insolatus McLachlan + Holocentropus dubis (Rambur) + Phryganea sp. (juv.) + Athripsodes aterrimus (Stephens) +Diptera Chaoboridae + Chironomidae Procladius sp. + + + +Orthocladiinae nd. + + + +Psectrocladius sp. + + + +Chironomus annularius Meigen + + Chironomus nuditarsis Strenzke + + Camptochironomus tentans (Fabricius) + Einfeldia spp. + +Cryptochironomus defectus Kieffer + + + +Dicrotendipes sp. + + + +Glyptotendipes gripecoveni Kieffer + + + +Polypedilum nubeculosum (Meigen) + + + +Polypedilum spp. (III group) + + + +Phaenopsectra sp. + +Microtendipes chloris (Meigen) + + Tanytarsus brundini Lindeberg + + + +Tanytarsus usmaenis Pagast + +Cladotanytarsus sp. + + +Paratanytarsus sp. + Chironomidae pupae + + Ceratopogonidae + + +Megaloptera Sialis lutaria (Linnaeus) + Coleoptera Donacia sp. +



34

Fig. 3. Sesonal variations of bethic macroinvertebrate biomass (year 2005).

Fig. 4. Sesonal variations of bethic macroinvertebrate biomass without molluscs (year 2005).


www.oandhs.org

35

The relationship between the occurrence of particular taxa and the kind of plant cover was found only in the case of some molluscs and Camptochironomus tentans larvae (Table 2, 3).

DISCUSSION

The fauna composition, especially Trichoptera (high frequency of Cyrnus crenaticornis), confirms mesotrophic status of Lake Łuknajno.

The number (1135 indiv. m-2) and biomass (8.876 g m-2) of zoobenthos in Lake Łuknajno were distinctly lower in comparison to the abundance of benthofauna of other shallow lakes in North Poland (Pieczyński 1977, Stańczykowska et al. 1983, Wiśniewski & Dusoge 1983, Dobrowolski 1994). In the shallow, macrophyte-dominated Lake Druzno, Giziński et al. (1997) recorded the density of zoobenthos that amounted to 12.2 thousands indiv. m-2 while the biomass of the community (without Mollusca) reached 25.7 g m-2

fresh weight. The main factors influencing benthos abundance in lakes are trophic and

oxygen conditions. However, near the shoreline, the depth, nature of bottom sediments, exposure to wave motion and degree of macrophyte development that can favour benthofauna growth are also crucial (Brinkhurst 1974, Stańczykowska et al. 1983, Cole & Wregmann 1983, Wiens & Rosenberg 1984, Rassmusen 1988, Dobrowolski 1994).

Table 3

Composition of macrobenthic comunity (without Insecta) at different sampling sites - (2004-2006)

Taxon Station number 1 2 3 4 OLIGOCHAETA + + + + HIRUDINEA Helobdella stagnalis (Linnaeus) + Erpobdella octoculata (Linnaeus) + + + MALACOSTRACA Asellus aquaticus (Linneus) + + + + GASTROPODA Viviparus contectus (Millet) + Valvata piscinalis (Linnaeus) + Bithynia tentaculata (Linnaeus) + Physa fontinalis (Linnaeus) + Lymnea peregra Muller + Lymnea stagnalis (Linnaeus) + Acroloxus lacustris (Linnaeus) + + BIVALVIA Pisidium casertanum (Poli) + Anadonta cygnea (Linnaeus) +



36

In spite of this, relatively low macrozoobenthos number was recorded in the shallow, macrophyte-dominated Lake Łuknajno. Low benthofauna abundance did not result from unfavourable trophic or oxygen conditions near the bottom (unpubl. results). Therefore, the negative impact of highly hydrated bottom sediments or the pressure of predators (ichtyofauna) should be considered. There would be possible anoxic conditions in lower layer of the sediment. The main component of inbenthos was Chironomidae larvae from genus Chironomus. They are characterized by high tolerance for anoxic condition and prefer sediments covered by charophytes (van den Berg et al. 1997). In Lake Łuknajno that kind of sediment was preferred by Camptochironomus tentans larvae. The relationship between the occurrence of particular taxa and the kind of plant cover was also found in the case of some molluscs.

The spatial distribution of benthofauna, considering its number, was uniform while the dynamics of changes was correlated with the life cycle of the insects that are the main component of the bottom zoocenosis.

ACKNOWLEDGMENTS

The author is grateful to prof. S. Czachorowski and dr P. Buczyński for Trichoptera verification and Odonata identification.

REFERENCES

Bowszys M., Hirsz E., Paturej E., 2006, The role of macrophytes in the diurnal distribution of crustacean zooplankton in a littoral of a shallow, macrophyte-dominated Lake, Electronic Journal of Polish Agricultural Universities, Biology, 9(2)

Brinkhurst R.O., 1974, The Benthos of Lakes, The Macmillan Press Ltd Cole R.A., Wregmann L.L., 1983, Relationship among zoobenthos sediments and organic matter

in littoral zones of Western Lake Erie and Saginaw Bay, J. Great Lakes Res., 9: 568-81 Dobrowolski Z., 1994, Occurrence of macrobenthos in different littoral habitats of the polymictic

Łebsko lake, Ekol. Pol. 42,1-2: 19-40 Ejsmont-Karabin J., Karabin A., Kornatowska R., Królikowska J., Ozimek T., 1996, The effect of

zooplankton on phosphorus cycling in shallow, hard-water and macrophyte-dominated lake, Ekol. pol., 44 (3-4): 259-70

Giziński A., Kentzer A., Rejewski M., 1997, Why does Druzno Lake (Poland) still exist? On the conditions of the pond ecosystem sustainability, Hydrobiologia, 342/343: 297-304

Karabin A., Ejsmont-Karabin J., Kornatowska R., 1997, Eutrophication procesess in a shallow, macrophyte-dominated lake – factors influencing zooplankton structure and density in Lake Łuknajno (Poland), Hydrobiologia, 342/343: 401-9

Królikowska J., 1997, Eutrophication procesess in a shallow, macrophyte-dominated lake – species distribution of submerged macrophytes in Lake Łuknajno (Poland), Hydrobiologia, 342/343: 411-16

Kufel L., Ozimek T., 1994, Can Chara control phosphorus cycling in Lake Łuknajno (Poland)?, Hydrobiologia, 275-276 (1): 277-83


www.oandhs.org

37

Kufel I., Kufel L., 1997, Eutrophication procesess in a shallow, macrophyte-dominated lake – nutrient loading to and flow through Lake Łuknajno (Poland), Hydrobiologia, 342/343: 387-94

Muirhead J.R., Ejsmont-Karabin J., Macisaac H.J., 2006, Quantifying rotifer species richness in temperate lakes, Freshwater Biology, 51(9): 1696-1709

Pieczyński E., 1977, Numbers and biomass of the littoral fauna in Mikołajskie Lake and in other Masurian lakes, Ekol. Pol., 25: 45-57

Rassmusen J.B., 1988, Littoral zoobenthic biomass in lakes, and its relationship to physical, chemical, and trophic factors, Can. J. Fish. Aquat. Sci., 45: 1436-47

Stańczykowska A., Jurkiewicz-Karnowska E., Lewandowski K., 1983, Ecological characteristics of lakes in north-eastern Poland versus their trophic gradient. X. Occurrence of molluscs in 42 lakes, Ekol. Pol., 31: 459-75

Wiens A. P., Rosenberg D. M., 1984, Effect impoundment and river diversion on profundal macrobenthos of Southern Indian Lake, Manitoba, Can. J. Fish. Aquat. Sci., 41: 638-48

Wiśniewski R. J., Dusoge K., 1983, Ecological Characteristics of lakes in north-eastern Poland. IX. The macrobenthos of 44 lakes, Ekol. Pol., 31: 429-59

van den Berg M.S., Coops H., Noordhuis R., van Schie J., Simons J., 1997, Macroinvertebrate communities in relation to submerged vegetation in two Chara-dominated lakes, Hydrobiologia, 342/343: 143-50




(39-47) 2007



Comparison of macroinvertebrate communities associated with

various habitats in anthropogenic reservoirs

Igor Jatulewicz1

Jan Długosz University of Częstochowa Institute of Chemistry and Environmental Protection

al. Armii Krajowej 13/15, 42-200 Częstochowa, Poland Key words: benthos, epifauna, submerged macrophytes, artificial substrate, clay pit, Częstochowa Upland

Abstract

The study was carried out in 2 clay-pits, located within the area of Częstochowa city (Southern Poland). Samples of macroinvertebrates were collected from bottom sediments, submerged plants and plastic rubbish. In the studied water bodies the similarity of invertebrate fauna determined to the family level was high (among 41 taxa found during studies 29 occurred in both pits). The lowest number of determined families (12 and 17 in reservoirs 1 and 2, respectively) and lowest values of Shannon-Weaver index were found for benthic communities while the highest values of both parameters were stated for fauna found on plastic rubbish. Some taxa such as Chironomidae and Hydracarina have the same abundance in all studied habitats.



July 05, 2007 December 06, 2007

I. Jatulewicz


40

INTRODUCTION

The composition, density and productivity of benthic invertebrate fauna were frequently studied in stagnant water bodies of various kinds whereas studies on fauna associated with plants were less frequent, although the significant role of hydrophytes for the composition and abundance of aquatic invertebrates has been known for a long time (Krecker 1939, Gurzęda 1959). Parallel studies on the two above mentioned cenoses are especially scarce (Kornijów 1996). Moreover, existing papers concerning peryphytic fauna usually deal with the epifauna of macrophytes whereas invertebrates living in freshwater on artificial substrates were rarely studied (Jeffries 1993, Czarnecka 2005).

In southern Poland the majority of stagnant water bodies is of anthropogenic origin: dam reservoirs, various kinds of pits (clay, sand or limestone), mining subsidence ponds or fish ponds. In the available literature there is abundant information concerning aquatic snails in those types of reservoirs. The most frequently studied water bodies were: dam reservoirs (Strzelec 2000), clay pits (Lewin 2001), gravel and sand pits (Strzelec and Serafiński 2004). However, these papers describe mainly fauna that inhabit macrophytes and other natural habitats.

This paper examines the invertebrate communities living on the bottom as well as on submerged plants and plastic rubbish in shallow parts of two reservoirs having similar trophy and similar composition of submerged plants but differing in the nature of the bottom.

STUDY AREA AND METHODS

The study was carried out in 2 clay-pits (Fig. 1), called “Adriatyk” (site 1) and “Bałtyk” (site 2), located within the area of Częstochowa city. They formed in 1960 as a result of the excavation flooding and nowadays serve as fishery and recreation reservoirs. The surface area of the analysed reservoirs, surrounded by meadows and mixed forest, reaches 5.5 ha (no 1) and 3.0 ha (no 2). The depth of both water bodies did not exceed 4.0 meters. The water level did not change during the investigation period suggesting that they both were supported by ground water. The biotope features of the analysed clay-pits were similar, however, the first reservoir had a high sandy landslip bank, while in the second one it was low and well consolidated what affected the bottom character of both investigated places (Table 1).

On each reservoir a single sampling site was located about 1 meter from the bank. Samples of macroinvertebrates were collected from April 2005 to November 2005, mainly at 1-month intervals. Single samples were taken from

macroinvertebrate communities in various habitats

www.oandhs.org

41

the approximately 225 cm2 of the bottom area using a bottom scraper with 0.3 mm mesh net and preserved in 4% formaldehyde. On the other hand, periphytic fauna was collected only qualitatively from the anthropogenic garbage left there for a long time (PET bottles, plastic materials, glass etc.) and from submerged vegetation, and then washed on a cuvette. Finally, all collected samples were sorted under a stereoscopic microscope. For the identification of molluscs, the key of Glöer and Meier-Brook (1998) was used. Percentage share of each taxon in three studied habitats was calculated. Trophic status of fauna was determined approximately taking into account only the main source of food (algivores, detritivores and predators). The significance of differences in the taxocen structure of communities was calculated using a non-parametric test (Mann-Whitney test) by STATISTICA 6.0 software package (STAT SOFT). In the water bodies, the following measurements were taken: temperature, pH, and

1

2

POLAND

N

“Adriatyk” pit

“Bałtyk” pit

Fig. 1. Location of the studied pits and the sampling sites (dots).

Table 1 Description of the investigated stations

Parameters Site 1 “Adriatyk” Site 2 “Bałtyk” pH 6.77 – 7.20 6.51 – 7.12 Cond. (µS) 112.36 – 464.9 105.9 – 577.5 Cl- (mg l-1) 19.0 – 23.0 22.5 –22.8 SO4

2- (mg l-1) 13.7 – 21.7 25.6 – 28.2 Depth (m) 0.5 0.5 Plants single tufts of submerged plants single tufts of submerged and emergent plants Character of the bottom sand and mud mud and detritus

I. Jatulewicz


42

conductivity. Water samples, for the identification of Cl-, SO42- content were

collected in September, October and November 2005, and the concentrations of ions were determined in the laboratory using capillary electrophoresis.

RESULTS

Physico-chemical characteristic of water

Water temperature varied from 24.1°C to 7.7°C. Almost neutral pH values were recorded at both sites (Table 1). The concentrations of chlorides and sulphates as well as conductivity values were similar in both pits being a little more variable in reservoir no 1.

Faunal diversity

A total of 3207 specimens were collected during the study. Taxonomical diversity calculated on the basis of all samples collected in each water body was similar: Shannon-Weaver index reached 3.36 at site no 1 and 3.54 at site no 2. One class (Oligochaeta), two orders (Ostracoda and Hydrachnellae) and 38 families were determined during studies (Table 2). The similarity of invertebrate fauna determined to family level was high – among 41 taxa found during the survey 29 were common to both pits. The most numerous were: Oligochaeta, Chironomidae and Planorbidae (site 1) and Caenidae (site 2). Moreover, Diptera, Coleoptera and Trichoptera were also diverse, whereas other insect groups like Odonata, Heteroptera, Pyralidae and Ephemeroptera were present in low species numbers. Contrary, crustaceans (Isopoda and Amphipoda) were not encountered. Thirteen families were represented by a few specimens only – each of these taxa did not exceed 0.1% of total fauna.

In the whole studied material 8 species of Gastropoda belonging to 5 families were determined, among them two alien species: Potamopyrgus antipodarum (J.E. Gray 1843) and Ferrissia clessiniana (Jickeli 1882). Four families: Ancylidae, Bithyniidae, Hydrobiidae and Lymnaeidae were represented by one species only, whereas family Planorbidae dominated in richness (4 species) and abundance. The highest number of Gastropoda species was revealed at site 1 (eight species on the rubbish and five on plants). Moreover, juvenile specimens from the families Bithyniidae, Lymnaeidae and Planorbidae were encountered there.

Fauna in various habitats

The lowest number of determined taxa (12 and 17 at sites 1 and 2, respectively) and the lowest values of Shannon-Weaver index were discovered


www.oandhs.org

43

for benthic communities while the highest ones were recorded for fauna collected from plastic rubbish (Table 2). Exclusively in this last habitat, taxa represented by a few specimens were also found (mainly Coleoptera, Heteroptera, some Diptera and Trichoptera) but generally the composition and structure of faunal communities living on plants and plastic rubbish were similar (Table 2) and differences were not statistically significant.

Table 2 The distribution of invertebrate fauna in studied reservoirs and habitats (expressed as percentage of particular taxa)

Site 1 Site 2 taxa bottom plants rubbish total bottom plants rubbish total Dendrocoelidae 1.2 1.5 0.8 0.1 0.3 4.3 1.4 Dugesiidae 0.3 0.5 0.3 Planaridae 1.0 0.3 Oligochaeta 74.1 15.2 9.5 36.6 47.2 17.4 15.4 31.7 Piscicolidae 0.1 0.1 Glossiphoniidae 0.2 0.1 Ostracoda 3.9 0.8 0.8 2.0 5.0 2.5 Coenagrionidae 0.8 0.2 0.2 0.1 0.7 0.6 0.4 Gomphidae 0.3 0.1 Caenidae 0.9 2.5 1.7 1.6 13.3 11.4 6.1 10.6 Baetidae 0.8 1.2 0.6 1.4 3.7 1.4 Dytiscidae 1.3 1.0 0.7 0.2 0.1 Curculionidae 0.2 0.1 Helodidae 1.0 2.3 1.1 2.0 4.0 1.6 Hydrophilidae 2.5 3.7 2.0 1.3 0.4 Dryopidae 0.5 0.1 Haliplidae 1.0 0.2 0.3 0.4 1.7 1.1 0.8 Polycentropodidae 1.1 0.1 Limnephilidae 0.2 0.1 Ecnomidae 0.3 1.3 0.5 0.7 0.3 3.6 1.7 Leptoceridae 0.2 0.2 0.1 0.3 0.2 0.1 Hydroptilidae 0.2 0.1 Naucoridae 0.2 0.1 0.8 0.3 Corixidae 0.9 0.3 0.2 0.5 0.6 0.3 0.4 Pleidae 0.2 0.1 3.1 0.4 0.7 Chironomidae 15.2 4.6 29.4 18.0 28.1 30.0 20.4 26.1 Ceratopogonidae 1.5 0.3 1.8 1.3 2.3 1.0 5.1 2.9 Sciomyzidae 0.3 0.1 Syrphidae 0.2 0.1 0.3 0.2 0.1 Limoniidae 0.5 0.3 0.2 0.2 0.1 Stratiomyidae 2.5 0.5 0.8 4.8 0.8 1.2 Rhagionidae 0.3 0.1 0.1 0.1 Ptychopteridae 1.0 1.0 0.6 1.7 1.7 0.8 Pyralidae 0.8 0.2 0.6 0.3 Sphaeriidae 1.2 0.5 0.1 0.1 Planorbidae 0.3 52.5 24.1 21.2 0.3 18.2 22.2 10.3 Ancylidae 0.2 0.1 0.1 1.0 4.0 1.5 Lymnaeidae 0.2 1.3 6.4 2.7 1.7 0.6 0.5 Bithyniidae 6.9 9.7 5.2 1.4 0.3 Hydrobiidae 0.2 0.1 Hydracarina 1.1 1.0 1.0 1.0 0.9 0.7 0.6 0.8 No of taxa 12 25 30 33 17 22 27 33 Shannon-Weaver index 2.09 2.89 3.29 2.53 3.39 3.36

I. Jatulewicz


44

Some taxa such as Chironomidae and Hydracarina were similarly abundant in all studied habitats, the occurrence of other taxa was connected with particular habitats – for example Turbellaria were usually present on plants and plastic objects while they were rarely found in benthic samples – the differences in frequency and number of the collected specimens in benthic and peryphitic samples were statistically significant (P<0.05).

At both sites Gastropoda were numerous among macrophytes and on artificial substrata, but on the bottom only 5 specimens were found. Moreover, particular species do not show specific habitat preferences. At site 1 the composition and abundance of Gastropoda inhabiting macrophytes and plastic rubbish were similar, except for Radix peregra, which dominated only on rubbish (Table 3). At site 2 six snail species were found on plants and five on rubbish (lack of Bithynia tentaculata), with the distinctive dominance of Armiger crista and Segmentina nitida. Juvenile specimens represented only family Planorbidae (Table 3).

Among Trichoptera only Ecnomus tenellus was fairly numerous in all

habitats, the occurrence of the remaining species was restricted to plants and especially plastic rubbish.

On plants and plastic rubbish algivorous taxa prevailed (Fig. 2) and their percentage share was similar in the both mentioned habitats (about 65% at site no 1 and below 55% at site no 2). Moreover, peryphitic detritivores were also abundant (22 – 35% of community). In the benthic communities this feeding group prevailed, and a very low percentage of predators was revealed (3.3 – 4.5%).

Table 3

Percentage of Gastropoda

Site 1 Site 2 GASTROPODA bottom plants rubbish total bottom plants rubbish total Bithynia tentaculata 10.04 23.9 18.7 6.0 2.1 Bithyniidae juv. 1.26 0.6 Radix peregra 1.67 11.3 6.4 7.5 2.5 4.2 Lymnaeidae juv. 7.95 3.8 Armiger crista 39.3 20.6 29.1 22.4 40.0 33.3 Gyraulus albus 12.5 24.3 18.1 1.5 1.7 1.6 Planorbarius corneus 0.4 0.2 Segmantina nitida 20.9 14.2 17.1 52.2 45.0 47.1 Planorbidae juv. >0.1 6.28 4.5 5.6 >0.1 6.0 3.3 5.3 Ferrissia clessiniana 0.4 0.2 >0.1 4.5 7.5 6.3 Potamopyrgus antipodarum 0.4 0.2


www.oandhs.org

45

DISCUSSION

The studied water bodies were formed more than 40 years ago (Gębicki et al. 2004) that is why the diversity and composition of the peryphitic fauna with the domination of Chironomidae, Oligochaeta and Gastropoda was similar to that described previously in the littoral of natural lakes partially overgrown by plants (Kornijów 1989; Chilton 1990; Olson et al. 1999; Pieczyńska et al. 1999). However, representatives of large taxa such as Isopoda (Asellus aquaticus) and Amphipoda (genus Gammarus) were absent what suggests that the colonization process was not finished or high predators pressure of invertebrates and fishes has been eliminating these fairly large taxa.

Due to the similar water trophy and the occurrence of almost the same plant species in both studied reservoirs, the composition of their epiphytic communities was similar. Also the composition and structure of communities living on plants and artificial substrates were almost the same - the differences between them were not statistically significant. At both sites, all collected snail species were rich in number. What is more, all identified species are common and frequently reported from anthropogenic reservoirs (Strzelec and Serafiński 2004) as well as from natural water bodies, e.g. lakes (Pieczyńska at al. 1999).

In contrast to the communities living on plants and plastic rubbish, differences in benthic fauna composition were stated exclusively as a result of different kind of the bottom in the studied reservoirs. Our studies, as well as experimental ones concerning colonization of various artificial substrata (Szlauer and Szlauer 1997, Schmude et al. 1998), showed that plastic rubbish are convenient substratum for fauna, and in a such habitat the density of

Fig. 2. Feeding groups of macroinvertebrates in various habitats.

I. Jatulewicz


46

invertebrates could be higher than in others. Also high diversity of invertebrates was recorded on plastic substratum (Czarnecka 2005). In the studied reservoirs taxa represented by a few specimens only (e.g. Planaridae, Curculionidae, Limnephilidae, Sciomyzidae and Hydrobidae) were found on plastic garbage - perhaps the colonization of such artificial habitat is easier than settling in a natural one. The preference of some taxa, e.g. Simuliidae, for inhabiting such items is occasionally known (Bokłak pers. com.). This kind of substrate may be used for studies of faunal diversity since it allows finding higher number of taxa than investigations made in other habitats.

Higher diversity of peryphitic invertebrate fauna in comparison with benthic fauna is reported (Czarnecka 2005, Kuflikowski 1986), but the parameters influencing such distribution are not studied in detail. Plants and artificial substrata provide more possibilities for hiding than bare bottom, some environmental parameters (oxygen content, food availability) are more favourable. Moreover, despite that invertebrate and fish predators (Diehl 1992) are numerous in these habitats, their effect on prey density is less visible than in pelagic zone (Koperski 1998).

ACKNOWLEDGEMENTS

We are deeply grateful to dr hab. Bronisław Szczęsny (Institute of Nature Conservation PAS, Kraków) for determination of Trichoptera larvae.

We would like to thank the students Aleksandra Krześlak and Marta Kuras for providing the materials collected during the preparation of their MSc thesis.

REFERENCES

Chilton E.W. 1990 – Macroinvertebrate communities associated with three aquatic macrophyte (Ceratophyllum demersum, Myriophyllum spicatum, and Vallisneria americana) in Lake Onalaska, Wisconsin - J. Freshw. Ecol. 5: 455 – 466.

Czarnecka M., 2005, Ekologiczny status epifauny zasiedlającej sztuczne podłoża podwodne. [Ecological status of epifauna settled on artificial submerged substrata], PhD thesis, Nicolaus Copernicus University, Toruń.

Diehl S. 1992 – Food choice by omnivorous fish – Ecology 73: 1646 - 1661. Gębicki C., Majchrzak B., Imiołek W., Jatulewicz I., Bokłak B., 2004, Waloryzacja Przyrodnicza

Parku Lisinieckiego w Częstochowie. Materiały niepublikowane, [Nature description of the Lisiniec Urban Park. unpablished], Akademia im. J. Długosza, Częstochowa.

Glőer P., Meier–Brook C., 1998, Süsswassermollusken - 12 Aufl., DJN, Hamburg, pp.136. Gurzęda A., 1959, Stosunki ekologiczne między fauną bezkręgową a roślinnością zanurzoną

[Ecological relationship between invertebrate fauna and submerged plants], Ekol. pol. seria B, 5, 139 – 145

Jeffries M., 1993, Invertebrate colonization of artificial pondweeds of differing fractal dimension - Oikos 67, 142 – 148.


www.oandhs.org

47

Koperski P., 1998, Co jedzą drapieżne owady litoralne? [What do the predatory, litoral insects eat?], Wiad. Ekol. 44, 95 – 130.

Kornijów R., 1989, Seasonal changes in the macrofauna living on submerged plants in two lakes of different trophy, Arch. Hydrobiol. 117, 49 – 60.

Kornijów R., 1996, O potrzebie równoległych badań nad fauną denną i naroślinną w płytkich siedliskach wód śródlądowych [On the need of simultaneous studies on benthic and epiphytic faunas in shallow habitats of inland waters], Wiad. Ekol. 42, 15-20.

Krecker F. H., 1939, A comparative study of the animal population of certain submerged aquatic plants, Ecology 20, 553 – 562.

Kuflikowski T., 1986, Development and structure of the Goczałkowice Reservoir ecosystem. XIII. Plant-dwelling fauna, Ekol. pol. 34, 473-489.

Lewin I., 2001, Zgrupowania ślimaków słodkowodnych (Gastropoda) w zbiornikach i ciekach Wysoczyzny Ciechanowskiej. Rozprawa na stopień doktora n. biol. [Freshwater snail communities in reservoirs and streams of Wysoczyzna Ciechanowska. PhD thesis]. Uniwersytet Śląski, Katowice, 267 pp.

Olson E.J., Engstrom E.S., Doeringsfeld M.R., Bellig R., 1999, The abundance and distribution of macroinvertebrates in relation to macrophyte communities in Swan Lake, Nicollet County, MN - http://files.dnr.state.mn.us/ecological_services

Pieczyńska E., Kołodziejczyk A., Rybak J. I., 1999, The responses of littoral invertebrates to eutrophication-linked changes in plant communities, Hydrobiologia 391, 9 – 21.

Schmude K. L., Jennings M. J., Otis K. J., Piette R. R., 1998, Effects of habitat complexity on macroinvertebrate colonization of artificial substrates in north temperate lakes, J. N. Am. Benthol. Soc. 17, 73-80.

Strzelec M., 2000, The changes in the freshwater snail (Gastropoda) fauna of the dam reservoir Gzel (Upper Silesia) and their causes, Folia Limnol. 7, 173-180.

Strzelec M., Serafiński W., 2004, Biologia i Ekologia Ślimaków w Zbiornikach Antropogenicznych. [The biology and ecology of gastropods in anthropogenic reservoirs], Centrum Dziedzictwa Górnego Śląska, Katowice, 90 pp.

Szlauer B., Szlauer L., 1997, Organisms colonizing polythene sheets deployed in Lake Miedwie (northwestern Poland), Acta Hydrobiol. 39, 111 – 119.




(49-54) 2007



Biomonitoring of the Łyna River (North Poland) in the years

1974-2006 on the basis of the benthic macroinvertrates

Lucyna Koprowska, Izabela Jabłońska–Barna1

Chair of Applied Ecology, Faculty of Environment Protection and Fisheries University of Warmia and Mazury

ul. Oczapowskiego 5, 10-957 Olsztyn, Poland

Key words: biomonitoring, river, pollution, macroinvertebrate, BMWP-PL

Abstract

This paper presents the changes in water quality of Łyna River in the years 1974-2006 based on benthic macroinvertebrates. To evaluate the environment quality the biological index BMWP-PL was used.

The analysis of the index values has shown the gradual improvement of the ecological condition in polluted sections of the river indicated by the increase in the macrofauna taxa number that has been observed since the 90’s. It was the effect of the construction of the sewage treatment plant and cutting off the inflow of wastewaters.

Water quality of the river reach upstream from the city has persisted on high or good status.



July 05, 2007 November 24, 2007

L. Koprowska, I. Jabłońska-Barna


50

INTRODUCTION

Biomonitoring can be defined as the use of biological responses to evaluate the changes in the environment with the intent to use this information in a quality control program (Rosenberg and Resh 1993, Kownacki et al. 2002). The oldest biological method of water assessment is the saprobic system of Kolkwitz and Marsson (1902, 1909), which is based on indicator species, also taking into account benthic invertebrates. This system was modified many times (Zelinka & Marvan 1961, Sladeček 1973, Friedrich 1990). At present, other methods of assessing water quality, the so-called biotic indices, are more often applied and based on higher taxonomic units (Armitage et al. 1983, De Pauw & Vanhooren 1983, Andersen et al. 1984, Lang & Reymond 1995). The most popular is the Biological Monitoring Working Party (BMWP) index, which was modified and applied in some European countries (Alba-Tercedor & Prat 1992). In Poland, this index (after modification) is also used for water quality assessment (Kownacki et al. 2004). Classification of water quality in rivers may be expressed as diversity index (Wihlm & Dorris 1968, Wihlm 1987, Kownacki 2000).

The main scope of this paper was to determine changes of water quality of the Łyna River near Olsztyn on the basis of the benthic invertebrates analysis using BMWP-PL index and diversity index in the period of 30 years (1974-2006). This analysis was also aimed at testing the usefulness of the Polish method of rivers water quality evaluation (Kownacki et al. 2004) in case of Łyna River.

STUDY AREA

The investigations were carried out at three sampling sites: 1 – upstream from Olsztyn, 2 – in the city centre, 3 – downstream from Olsztyn in the City Forest (Fig. 1). Now, the upper reaches of river (the sites 1–2) is regulated. The banks of the river are strengthened with natural elements and the river bottom has a uniform character. The river is not regulated at the site 3.


Materials were collected in 1996, 2003, 2004 and 2006. Additional published data on the materials collected in 1974 and 1978 (Wielgosz 1979, Wielgosz et al. 1982) were included in the analysis. The methods used in both sets of data were similar, so comparisons could be made. The evaluation of water quality was executed on the basis of two criteria: the value of a index BMWP–PL and the value of biodiversity index d (Kownacki et al. 2004).

Biomonitoring of the Łyna River

www.oandhs.org

51

BMWP–PL score was calculated according to a standard chart BMWP-PL.

The index of biodiversity (d) was calculated according to the formula: where: s – number of families found; N – total density (ind. m-2) of

macroinvertebrates at the given sampling site.


On the investigated reach of the Łyna River 53 taxa of invertebrates (52 families and one class Oligochaeta) were found (Table 1). The number of taxa was different at each site and in particular years, and oscillated between 2 - 6 taxa at polluted sites in the 70’s and 80’s and 20–33 at unpolluted sites (Table 1).

N logsd =

Fig. 1. Location of the sampling sites; 1-3 – site numbers.



52

Table 1 Composition of benthic invertebrate and water quality of the Łyna River near Olsztyn

1974* 1978** 1996 2003 2004 2006 Date Taxa

1 2 3 1 2 3 1 2 3 1 2 3 1 2 3 1 2 3

Beraeidae 10 + + + +Leptoceridae 10 + + + + Molannidae 10 + Taeniopterygidae 9 + Aphelocheiridae 7 + + + + Calopterygidae 7 + + + + + + + + + + + + +Caenidae 7 + + + + + + Dreissenidae 7 + + Ephemeridae 7 + + Ephemerellidae 7 + Gomphidae 7 + + + Leptophlebiidae 7 + Leuctridae 7 + Limnephilidae 7 + + + + + + + + + + + +Unionidae 7 + + + + + + + + Viviparidae 7 + + + + + + + + Baetidae 6 + + + + + + + +Bithyniidae 6 + + + + + + + + Coenagrionidae 6 + + + Ecnomidae 6 + Gammaridae 6 + + + + + + + + + + + Heptageniidae 6 + + + Hydroptilidae 6 + Neritidae 6 + + + + Piscicolidae 6 + + + + + + Platycnemidae 6 + + +Polycentropodidae 6 + + + + + + Simuliidae 6 + Corixidae 5 + + + + + + + + +Dytiscidae 5 + + + + + + +Gyrinidae 5 + + + + + + +Haplidae 5 + + + + + + +Hydroptilidae 5 + + Hydropsychidae 5 + + + + + + Nepidae 5 + + + + +Notonectidae 5 + Tipuliidae 5 + Ceratopogonidae 4 + + + + + + Planorbidae 4 + + + + + + + Sphaeriidae 4 + + + + + + + + + + Valvatidae 4 + + + + + + + + Ancylidae 3 + + Asellidae 3 + + + + + + + + + + + + +Chironomidae 3 + + + + + + + + + + + + + + + +Erpobdellidae 3 + + + + + + + + + + + + + + + +Glossiphonidae 3 + + + + + + + + + + + + Hirudinidae 3 + Lymnaeidae 3 + + + + + + + + + Physidae 3 + + + + Sialidae 3 + + + + + + + +Culicidae 2 + + + +Oligochaeta 2 + + + + + + + + + + + +Psychodidae 1 + Number of taxa 29 6 4 21 6 2 18 22 15 33 23 21 18 18 19 18 17 16

BMWP-PL I IV IV I IV V II I II I I I I II II II II IId I IV V I III V I I I I I I II II II II II II

General classification I IV V I IV V II I II I I I II II II II II II of water quality

* Wielgosz (1979) ** Wielgosz et al. (1982)

Biomonitoring of the Łyna River

www.oandhs.org

53

The values of the biotic index BMWP–PL and biodiversity index d have classified the Łyna river’s water in a range from very clean (class I – high status) to very polluted (class V – bad status) (Table 1). In the 70’s and 80’s at site 1, situated upstream from Olsztyn, based on benthic invertebrates, the water quality of the Łyna River was high – class I. The taxonomic composition of benthic invertebrates was characteristic of natural lowland rivers. During this period of time at sites 2 and 3 located in the city area and downstream, the water quality was bad – poor status (class IV) at site 2 and very bad (class V) at site 3. The composition of fauna was characteristic for strongly polluted rivers with Oligochaeta and Chironomidae dominance as well as some leeches from the Erpobdellidae and Glossiphonidae families. Since the second half of the 90’s, after the wastewater treatment plant in Olsztyn was built, the water quality at sites 2 and 3 has clearly improved. This reach of the river obtained a good status (class II), and in 2003 even a high status (class I). Clean water taxa like: Ephemeroptera, Trichoptera, Bivalvia reappeared in the river. However, the water quality in the Łyna River upstream from Olsztyn in the 90’s became worse (class II), excluding the year 2003 (class I). Probably the reason for this was the transformation of biotic and abiotic relations at the river bottom, which are the result of regular dredging and the cutting of macrophytes, and not the deterioration of water quality.

According to Semanchenko and Moroz (2005), the biological index BMWP is very sensitive. On the basis of the results from 1974–2006 it might be confirmed that the BMWP–PL is also a good method to show changes in environment. This method can be useful for determining ecological status of different types of running waters (Dumnicka et al. 2006). The biological index BMWP–PL correlates with other biological indices and chemical variables (Czerniawska–Kusza 2005).

REFERENCES

Alba-Tercedor J., Prat J.N., 1992, Spanish experience in the use of macroinvertebrates as biological pollution indicators, In: Newman, P.J., Piavaux M.A., Sweeting R.A. (eds). River Water Quality. Ecological Assessment and Control. Commission of the European Communities, Brussels, 733-38

Andersen M.M., Riget F.F., Sparholt H., 1984, A modification of the Trent Index for use in Denmark, Water Res., 18: 145-51

Armitage P.D., Moss D., Wright J.F., Furse M.T., 1983, The performance of new biological water quality score system based on macroinvertebrate over a wide range of unpolluted running-water sites, Water Res., 17: 333-47

Czerniawska-Kusza I., 2005, Comparing modified biological monitoring working party score system and several biological indices based on macroinvertebrates for water-quality assessment, Limnologica, 35: 169-76



54

De Pauw N., Vanhooren G., 1983, Method for biological quality assessment of watercourse in Belgium, Hydrobiologia, 10: 153-68

Dumnicka E., Jelonek M., Klich M., Kwandrans J., Wojtal A., Żurek R. 2006. Ichthyofauna and ecological status of Vistula, Raba, Dunajec and Wisłoka Rivers. Ins. Nature Conserv., Pol. Acad. Sc., Kraków, pp. 219

Friedrich G., 1990, Eine Revision des Saprobiensystems, Z. Wasser-Abwasser-Forsch., 23: 141-52

Grzybowski M., Endler Z., 2006, Ecomorphological evaluation of Łyna River in borderline of the Olsztyn city, ZN AR Kraków, Inżynieria Środowiska, 28 – in press

Kolkwitz R., Marsson M., 1902, Grundsätzliches für die biologische Beurteilung des Wassers und seiner Flora und Fauna, Mit. Königl. Prüfugsant. Wasser, Abwasser, 1: 33-72

Kolkwitz R., Marsson M., 1909, Ökologie der tierischen Saprobien. Beitrage zur Lehre von biologischen Gewässerbeurteilung, Int. Rev. Ges. Hydrobiol, Hydrogr., 2: 126-52

Kownacki A., 2000, Diversity of benthic macroinvertebrates as a monitoring method for polluted rivers, Acta Hydrobiol., 42, 3/4: 207-14

Kownacki A., Soszka H., Kudelska D., Fleituch T. 2004. Bioassessment of Polish rivers based on macroinvertebrates. In: Geller W. et al. (eds). 11th Magdeburg seminar on Waters in Central and Eastern Europe: Assessment, Protection, Management. Proceedings of the international conference, 18-22 October 2004 at the UFZ. UFZ-Bericht, 18/2004: 250-251.

Kownacki A., Soszka H., Fleituch T., Kudelska D., 2002, The ecological assessment of river quality in Poland on the basis of communites of benthic invertebrates, [In:] Kownacki A., Soszka H., Fleituch T., Kudelska D. (eds) : River biomonitoring and benthic invertebrates communities (monography), Institute of Environmental Protection, Karol Starmach Institute of Fresh water Biology Pol. Acad, Sc., Warszawa – Kraków, 71- 88

Lang C., Reymond O., 1995, An improved index of environmental quality of Swiss rivers based on benthic macroinvertebrates, Aquatic Sciences, 57, 172-180

Rosenberg D.M, Resh V.H. (eds), 1992, Freshwater biomonitoring and benthic macroinvertebrates, New York, London, Chapmant & Hall, pp. 488

Semenchenko V.P., Moroz M.D., 2005, Comparative analysis of biotic indices in the monitoring system of running water in a biospheric reserve, Water Res., 32(2): 223-6

Sládeček V., 1973, System of water quality from the biological point of view, Arch. Hydrobiol. Beih. Ergebn. Limnol., 7: 1-218

Wielgosz S., 1979, The effect of waters from the town of Olsztyn on invertebrate communities in the bottom of the River Łyna, Acta Hydrobiol., 21: 149-65

Wielgosz S., Żółtowski G., Kuklińska B., 1982, The effect of organic sewage on the lithon zoocenosis in the Łyna River, Ekol. Pol., 30: 187-203

Wihlm J.L., 1987, Comparison of some diversity indices applied to populations of benthic macroinvertebrates in stream receiving organic wastes, J. Water Poll. Control Federation, 39: 1673-83

Wihlm J.L., Dorris T.C., 1968, Biological parameters for water quality criteria, Bio Science, 18: 477-81

Zelinka M., Marvan P., 1961, Zur Präzisierung der biologischen Klassifikation der Reinheit fliessender Gewässer, Arch. Hydrobiol., 57: 389-407




(55-61) 2007



The effect of selected environmental factors on the occurrence

of macroinvertebrates in the Osownica River

Małgorzata Korycińska1, Elżbieta Królak

Department of Ecology and Environmental Protection University of Podlasie, ul. Prusa 12, 08-110 Siedlce, Poland

Key words: macroinvertebrates, chemical parameters, bottom sediments, lowland river

Abstract

Taxonomic composition of macroinvertebrates was analysed in a small lowland river and confronted with selected chemical properties of water and bottom sediments. No distinct differences were found in the chemical properties of water between studied sites. The content of organic carbon (TOC), total nitrogen (TN) and total phosphorus (TP) in bottom sediments was associated with the type of substratum. Nutrient concentrations were low (TOC < 0.4%, TN < 0.4 mg g-1 dry wt., TP < 0.15 mg g-1 dry wt.) at sites of sandy or stone-sandy substratum. These sites were dominated by insect larvae. In sites of sandy-silty or silty substratum with a large content of detritus and nutrients, the dominating taxa were Asellidae, Mollusca, Oligochaeta and Erpobdellidae, and from among insect larvae - Limnephilidae and Sialidae.



July 05, 2007 December 07, 2007

M. Korycińska, E. Królak


56

INTRODUCTION

Information on taxonomic composition of macroinvertebrates in small rivers in Poland is relatively scarce. For practical reasons, i.e. for the assessment of water quality, the monitoring programmes are usually carried out in large rivers. At present this assessment is made according to the requirements of the Water Framework Directive (Directive 2000/60/EC) with the use of invertebrate macrofauna (Ordinance 2004, Kownacki et al. 2004). Most macroinvertebrates used in biotic indices (De Pauw & Vanhooren 1983, Extence et al. 1987) are the benthic organisms dwelling in surface layers of bottom sediments. Chemical composition of substratum, apart from river water quality, seems thus an important factor that determines the occurrence of aquatic macroinvertebrates.

The study presented in this paper was aimed at estimating the taxonomic composition of macroinvertebrates in a small lowland river against a background of selected chemical parameters of water and bottom sediments.


The study was carried out in the Osownica River on Środkowomazowiecka Lowland. The river of a length of 45 km flows through the area of Nadbużański Landscape Park. Along many stretches the river is regulated and joined to the system of reclamation ditches. The catchment basin of the river is mostly agricultural.

The studies were carried out in 2006, at 4 sites situated along the river course. Site 1 was situated in the upper course of the river, the bottom was sandy there. Site 2 situated at 30th km of the river length was characterised by a sandy-silty bottom with a large content of detritus. Site 3 selected at 16th km of the river length had a silty bottom which turned into gravel in some places. Site 4 was located in the outlet stretch of the river; the bottom changed from stony to sandy, then to silty. Water depth at sampling sites ranged from 0.3 – 0.7 m, flow velocity: 0.4 – 0.5 m s-1. Water, bottom sediments and macroinvertebrates were collected three times: in May, September and at the end of October.

Concentration of oxygen, BOD5, nitrates, ammonium, phosphates, calcium, chlorides, pH and electrolytic conductivity in water were measured with the standard methods adopted in Poland. Macroinvertebrates were collected with the semi-quantitative method using a grab sampler from an area of 1 m2. Sampling procedure involved various habitats at a given site. The collected material was washed on a sieve of 0.5 mm mesh size. Macroinvertebrates were taxonomically determined to the family level with the help of available keys and publications. From the same sites 4-6 samples of bottom sediments were taken with the core sampler of 8 cm diameter. pH in 1 M KCl, organic carbon with the

The effect of selected environmental factors on the occurrence of macroinvertebrates

www.oandhs.org

57

Tiurin’s method (Ostrowska et al. 1991), total phosphorus with the molybdenum blue method (Standard Methods 1999) and total nitrogen with the phenylhypochlorite method (Solórzano 1969) were determined in samples of bottom sediment.

RESULTS

No marked differences were found in the chemical parameters of water between particular sites. Water pH varied from 7.1 to 7.5, conductivity from 0.385 to 0.414 mS cm-1, dissolved oxygen from 7.53 to 10.33 mg dm-3, BOD5 from 4.27 to 5.27 mg O2 dm-3, phosphates from 0.27 to 0.47 mg dm-3, nitrates from 1.50 to 2.77 mg dm-3, ammonium ions from 0.23 to 0.63 mg dm-3, chlorides from 14.2 to 17.3 mg dm-3, and calcium ions from 63.0 to 69.8 mg dm-3. Significant differences were found, however, in the chemical composition of bottom sediments. Mean values of pH ranged from 6.53 to 7.35, organic carbon – from 0.30 to 4.99%, total nitrogen – from 0.18 to 5.94 mg g-1 dry wt., total phosphorus - from 0.10 to 2.76 mg g-1 dry wt. In sites 2 and 3 an elevated content of organic carbon was accompanied by higher concentrations of total N and P (Fig. 1) and lower pH of bottom sediments. Mean estimated density of macroinvertebrates at these two sites was c. 500 ind. m-2. Crustacea represented by Asellidae were the dominating taxa at these sites; their

Fig. 1. Mean density (number of individuals m-2) of macroinvertebrates and mean values of total nitrogen and total phosphorus at the sites in the Osownica River.



58

percentage contribution to the total density of macroinvertebrates was 55.2 and 34% at sites 2 and 3, respectively. Less numerous were insects and their larvae, the latter dominated by Limnephilidae and Sialidae. In sites 2 and 3 their percentage contributions were 21.7% and 32.9%, respectively. Considerable percentage shares (c. 15%) showed also Annelida represented by Erpobdellidae and Oligochaeta.

Smaller density of macrofauna was noted at sites 1 and 4 (323 and 104 ind. m-2, respectively) where the organic carbon content did not exceed 0.4%, total N was less than 0.4 mg g-1 and total P was less than 0.15 mg g-1. The macrofauna was dominated by insects and their larvae contributing 94.3% and 81.5% to the total number of macroinvertebrates at sites 1 and 4, respectively (Fig. 1). The presence of Plecoptera was recorded among collected insects (Fig. 2). Ephemeroptera represented mainly by Ephemeridae were very numerous at site 1. In site 4 the density of Gomphidae (Odonata) and Leuctridae (Plecoptera) larvae was highest from among all studied sites. The number of determined macroinvertebrate families in the Osownica River was 26 at sites 2 and 4, 30 at site 3 and 33 at site 1.

DISCUSSION

The occurrence of macroinvertebrates in running waters is affected by various factors, i.a. water quality parameters, type of substratum and its chemical composition, water velocity and the presence of aquatic macrophytes (e.g. Allan 1998; Hofmann, Mason 2005; Hus et al. 2006; Pliŭraite, Kesminas

Fig. 2. Mean density (number of individuals m-2) of Insecta and its larvae at the sites in the Osownica River.


www.oandhs.org

59

2004; Whiles, Dodds 2002; Wright et al. 1994; Yuan 2004). The habitat of river macroinvertebrates is a combination of all these factors.

Chemical analyses of waters of the Osownica River did not show marked differences in the concentration of parameters between the sites. Most of determined chemical parameters (pH, conductivity, oxygen concentration, chloride ions and nitrate concentrations) were within the norms characteristic of waters of the 1st quality class. The concentration of calcium ions was typical of waters of the 2nd quality class while phosphate ions concentration of 2nd and 3rd quality class waters. The final classification of waters at all sites in the Osownica River was determined by BOD5 values which corresponded to the norms of the 3rd quality class.

Much greater differences were found in nutrient concentrations between analysed bottom sediments. The content of organic carbon, TP and TN was closely associated with the type of substratum. The highest concentrations of these elements were noted at sites 2 and 3 (Fig. 1) with sandy-silty bottom rich in detritus (site 2) or silty bottom (site 3). Both sites were abundant in Asellidae, larvae of Limnephilidae whose many representatives are detrivores (Czachorowski, Pietrzak 2003) and Sialidae tolerating high concentrations of phosphorus (Yuan 2004). Filtrators represented mainly by Sphaeriidae, Hydropsychidae and Simuliidae were also numerous. Molluscs as typical filtrators need more fertile habitats for living (Hus et al. 2006, Piechocki 1991). Statistically significant correlation between the concentration of organic carbon, TN and TP in sediments and the density of molluscs (r = 0.7669, 0.5807, 0.7648, respectively, p<0.05, n=12) confirms this relationship. As in the case of molluscs, statistically significant correlation was found between the density of Diptera represented mainly by Simuliidae and the content of organic carbon (r=0.6439) and total P (r=0.6363). Close relationship between the content of organic matter and the presence of caddis flies of the family Hydropsychidae was also noted by Whilles and Dodds (2002) and by Pliŭraite and Kesminas (2004).

Higher densities of insects and insect larvae were found at sites situated in the upper and lower course of the river. These sites had sandy bottom (site 1) or stony-sandy bottom which in some places turned out into silt. Sandy bottom (site 1) appeared suitable for numerous Ephemeroptera (Fig. 2), mainly Ephemeridae. This family is known to prefer sandy sediments (Allan 1998; Elexová, Némethová 2003; Kołodziejczyk, Koperski 2000; Schloesser et al. 2000). Stony substratum favours the occurrence of macroinvertebrates due to its better stability (Allan 1998; Miserendino 2001; Pliŭraite, Kesminas 2004). Large stones and sunken tree trunks are suitable habitats for larvae of many species of Plecoptera, Ephemeroptera and Trichoptera (Riedel, Majecki 1994; Szczęsny 1995; Miserendino 2001). In the Osownica River the highest density of Plecoptera was found at site 4, Odonata represented mainly by Gomphidae were also numerous. These groups of animals are the rheophilic taxa



60

(Kittel 1991, Buczyński et al. 2006). Both Plecoptera and Odonata were more numerous at sites 1 and 4,which were poor in organic carbon, TN and TP.

The results of this study do not fully confirm the literature data (e.g. Allan 1998; Pliŭraite, Kesminas 2004), according to which higher densities of macrofauna are noted on stony than on sandy bottom. In the Osownica River higher densities of macrofauna were found on sandy substratum (site 1) than on stone-sandy substratum of site 4. No marked differences were also noted in the diversity of estimated taxa – the number of families ranged from 26 to 33. More information on habitat preferences among determined families of macroinvertebrates would bring the identification of organisms to species. There are species within any family which markedly differ in their habitat preferences (Czachorowski, Piotrowska 2006; Pliŭraite, Kesminas 2004; Szczęsny 1990).

The results of this study showed that the type of substratum and consequently the content of organic carbon, total N and total P exerted a stronger impact on the composition of macrofauna community in the Osownica River than chemical properties of river waters. The latter did not vary as much as did the chemical parameters of bottom sediment.

REFERENCES

Allan J. D., 1998, Stream Ecology. Structure and Function of Running Waters, Wyd. Naukowe PWN, Warszawa (in Polish), pp. 450

Buczyński P., Lewandowski K., Wissig N., 2006, Materials to the knowledge of dragonflies(Odonata) of the River Narew valley in the vicinity of Drozdowo (north-eastern Poland), Drozdowskie Zeszyty Przyrodnicze, 3: 5-12

Czachorowski S., Piotrowska K., 2006, Caddis flies in the Narew River’s valley between Wizna and Łomża – an ecological characteristic of distrubation, Drozdowskie Zeszyty Przyrodnicze, 3: 13-35

Czachorowski S., Pietrzak L., 2003, A guide for identification of caddis-flies (Trichoptera) occurring in Poland. Larvae, Wydawnictwo Mantis, Olsztyn, pp. 32

De Pauw N., Vanhooren G., 1983, Method for biological quality assessment of watercourses in Belgium, Hydrobiol., 100 : 153-68

Directive 2000/60/EC of the European Parliament and of the Council of 23 Oct. 2000 establishing a framework for Community action in the field of water policy, OJEC L 327/1 of 22.12.2000

Elexová E., Némethová D., 2003, The effect of abiotic environmental variables on the Danube macrozoobenthic communities, Limnologica, 33: 340-54

Extence C.A., Bates A.J., Forbes W.J., Barham P.J., 1987, Biologically based water quality management, Environmental Pollution, 45: 221-36

Hofmann T. A., Mason Ch. F., 2005, Habitat characteristics and the distribution of Odonata in a lowland river catchment in eastern England, Hydrobiol., 539: 137-47

Hus M., Śmiałek M., Zając K., Zając T., 2006, Occurrence of Unio crassus (Bivalvia, Unionidae) depending on water chemistry in the foreland of the Polish Carpathians, Polish Journal of Environmental Studies, 15: 169-72

Kittel W., 1991, Stoneflies (Plecotera) of the Świętokrzyskie Mountains, Fragm. Faun. 35: 31-47 (in Polish)


www.oandhs.org

61

Kołodziejczyk A., Koperski P., 2000, Freshwater invertebrates of Poland. A guide for the identification and basis of biology and ecology of macrofauna, Wyd. Uniwersytetu Warszawskiego. Warszawa, pp. 249 (in Polish)

Kownacki A., Soszka H., Kudelska D., Fleituch T., 2004, Bioassessment of Polish rivers based on macroinvertebrates, [in:] Proceedings of the 11th Magdeburg seminar on waters in central and eastern Europe: assessment, protection, management, Leipzig 18-22.10. 2004. Eds. Geller W. et al., UFZ Leipzig-Halle: 250-251

Miserendino M.L., 2001, Macroinvertebrate assemblages in Andean Patagonian rivers and streams: environmental relationships, Hydrobiol., 444: 147-58

Ordinance of the Minister of Environmental Protection of 11 Feb. 2004 concerning the classification which is used to present surface and underground waters state, and the ways of monitoring, interpreting the results and presenting the waters statuse, Dz.U. Nr 32, poz. 283 and 284, 1729-42, (in Polish)

Ostrowska A., Gawliński S., Szczubiałka Z., 1999, The methods of the analysis and the assessment of soils and plants properties, Katalog Inst. Ochr. Środ., Warszawa, pp. 334

Piechocki A., 1991, Systematics, biology and ecology of the pill-clams (Pisidium Pfeiff.) (Bivalvia, Eulamellibranchia), Acta Univ. Lodz., Folia limnol., 4: 3-31

Pliŭraite V., Kesminas V., 2004, Species composition of macroinvertebrates in medium-sized Lithuanian rivers, Acta Zoologica Lithuanica, 14(3): 10-25

Riedel W., Majecki J., 1994, Caddisflies (Trichoptera) of Roztocze, Fragm. Faun., 37, 315-22 Schloesser D. W., Krieger K. A., Ciborowski J. J. H., Corkum L. D., 2000, Recolonization and

possible recovery of Burrowing Mayflies (Ephemeroptera: Ephemeridae: Hexagenia spp.) in Lake Erie of the Laurentian Great Lakes, J. Aquat. Ecosyst. Stress and Recovery, 8: 125-41

Solórzano L., 1969, Determination oh ammonia in natural waters by the phenylhypochlorite method, Limnnol. Oceanogr., 14: 799-800

Standard Methods for the Examination Water and Wastewater, 1999, Eds. Clescerl, L. S., Greenberg, A. E., Eaton, A. D., Am. Publ. Health Assoc., New York, pp. 1325

Szczęsny B., 1990, Benthic macroinvertebrates in acidified streams of the Świętokrzyski National Park ,Central Poland), Acta Hydrobiol. 32: 156-69

Szczęsny B., 1995, Degradation of benthic invertebrate fauna of the Dunajec River in the neighbourhood of Pieniny National Park (Southern Poland), Ochrona Przyrody, 52, 207- 24 (in Polish)

Yuan L.L, 2004, Assigning macroinvertebrate tolerance classifications using generalised additive models, Freshwater Biology, 49, 662-67

Whiles M.R., Dodds W.K., 2002, Relationships between stream size, suspended particles, and filter-feeding macroinvertebrates in a Great Plains Drainage Network, Journal of Environmental Quality, 31(5), 1589-1600

Wright J.F., Blacburn J.H., Clarke R.T., Furse M.T., 1994, Macroinvertebrate-habitat associations in lowland rivers and their relevance to conservation, Verh. Internat. Verein. Limnol.. 25, 1515-18




(63-71) 2007



The influence of the sewage treatment plant in Międzyrzec Podlaski on the Krzna River (eastern Poland) water quality

Elżbieta Królak1, Małgorzata Korycińska, Aleksandra Michaluk

Akademia Podlaska, Instytut Biologii Katedra Ekologii i Ochrony Środowiska

ul. Prusa 12, 08-110 Siedlce, Poland Key words: lowland river, macroinvertebrates, BMWP-PL biotic index, chemical data

Abstract

The paper presents the results of studies on the influence of wastewaters discharged from the sewage treatment plant in Międzyrzec Podlaski on water quality of the Krzna River. Based on the results of measurements of selected chemical parameters of water and biological indices based on macroinvertebrate taxonomic composition it was found that the influx of wastewaters from the sewage treatment plant lowers the values of chemical indices of water, increases the density of macrofauna, especially of Oligochaeta and Erpobdellidae, lowers the number of macroinvertebrate families and the value of the BMWP-PL index. The quality of the Krzna River water improves significantly 5 km downstream the outlet of wastewaters from the sewage treatment plant.

1 corresponding author: [email protected]


July 05, 2007 November 16, 2007

E. Królak, M. Korycińska, A. Michaluk


64

INTRODUCTION

One of the factors considered in ecological assessment of rivers quality is taxonomical composition of macroinvertebrates, which is recommended by Water Framework Directive (Directive 2000). Effluent discharge from sewage treatment plants influences the taxonomic composition and diversity of macroinvertebrates in rivers (e.g. Kornijów, Lachowska 2002; Stańczykowska et al. 2002; Fleituch et al. 2002). Oligochaeta and Chironomidae are the most numerous among all macroinvertebrates behind the discharge from sewage treatment plants (Kornijów, Lachowska 2002; Kownacki et al. 2002). The quality of rivers in Poland and their ability to self–purification are directly related to the pollution load discharged into the rivers. Our studies were carried out in the lowland Krzna River (eastern Poland) polluted by wastewaters from the sewage treatment plant in Międzyrzec Podlaski. The aims of the study were: - chemical characteristics of wastewaters discharged from the sewage

treatment plant and water of the Krzna River at three sampling sites located: upstream of the discharge of wastewaters from the sewage treatment plant and below that point, 200 m and 5 km from it,

- the analysis of the taxonomic composition of macroinvertebrates in the Krzna River,

- the assessment of the influence of wastewaters discharged from the sewage treatment plant on the quality of the Krzna water.

STUDY AREA

The Krzna River is the left-bank tributary of the Bug River (Fig. 1). It is about 120 km long and the catchment area of the river is 3353 km2. The river flows through Polesie Podlaskie and South Podlasie Lowland (Kondracki 1998) in the Lublin Province. According to the Water Framework Directive, the Krzna River is classified to the 16th ecoregion (Directive 2000). It is a naturally meandering river; its bed was hydrologically regulated only in some parts. Wastewaters from the sewage treatment plant in Międzyrzec Podlaski are discharged into the Krzna River (about 67 km from its mouth). The treatment plant itself deals mainly with municipal wastes which are mechanically and biologically treated with the advanced reduction of phosphate and nitrate ions. The throughput of the treatment plant is 1400 m3 a day. The sewage is discharged into the river through the canal which is 1 km long.

The influence of the sewage treatment plant on river water quality

www.oandhs.org

65


The samples for chemical analyses were collected from 3 sites located at the Krzna and 1 site located in the discharge canal. The river was 13 – 16 m wide, and about 0.5 – 1.0 m deep in parts where the sampling sites were located. Site 1 was located upstream of the discharge canal where the bottom substrate of the river was sandy. Site 2 was located 200 m below the point of discharge of wastewater from the treatment plant; the bottom substrate in that part of the river was muddy. Site 3 was located 5 km below the discharge point where the bottom substrate was sandy-muddy. The discharge canal was 1 m wide and 0.5 m deep. Its bottom was concreted and covered with a thin layer of mud. The samples were taken four times, from April to November 2006.

The following parameters were determined in the water taken from the Krzna River and the discharge canal: BOD5, nitrate, ammonium, phosphate, calcium and chloride ion concentration, oxygen concentration, pH and electrolytic conductivity.

Biological analyses included macroinvertebrate samples collected with the semi-quantitative method, with a 0.2 m wide drag. The sampling procedure covered all

Fig. 1. Study area of the Krzna River.



66

the habitats at each site (including the riffles, current, plants and the different bottom substrata). 5 sub-samples were taken at each sampling site of a bottom surface of about 1 m2 (each of the sub-samples from the surface of about 0.2 m2). The collected material was washed in a sieve of 0.5 mm mesh size. Taxonomic identification of macroinvertebrates was done to family level. The results of macroinvertebrate community analysis were used for the biological assessment of the Krzna River water using the BMWP-PL index adopted for the assessment of Polish rivers water quality (Kownacki et al. 2004, Ordinance 2004).

RESULTS

Among four sampling sites, the highest ammonium, nitrate, calcium and chloride ion concentrations, and the highest values of BOD5 and electrolytic conductivity were noted in the canal used to discharge wastewater from the treatment plant. On the other hand, the phosphate ion concentration was the lowest in the discharge canal. The influx of wastewater from the treatment plant had insignificant effect on the chemical parameters of the Krzna River water (compare the data from site 1 and site 2) (Table 1). At the site located 200 m downstream from the discharge canal the greatest number of macroinvertebrates

was noted; the average macroinvertebrate density measured during the study period at the site was about 276 individuals m-2. At other sites located in the river the average density of macroinvertebrates was about 150 individuals m-2 (site 3) and 160 individuals m-2 (site 1). At the site located 200 m below the discharge canal, annelids were the most numerous of all macroinvertebrates.

Table 1

Mean values (±SD) of selected chemical parameters of the Krzna River water and of the wastewater from the discharge canal of the sewage treatment plant in Międzyrzec Podlaski

site parameter 1 - Krzna canal 2- Krzna 3 – Krzna pH 7.29 ±0.25 7.4 ±0.33 7.38 ±0.30 7.32 ±0.43 electrolytic conductivity mS cm-1 0.545 ±0.068 1.197 ±0.058 0.581 ±0.070 0.536 ±0.036 O2 mg dm-3 8.55 ±1.62 7.3 ±1.79 8.05 ±2.22 8.60 ±2.00 BOD5 mg O2 dm-3 1.87 ±0.93 3.87 ±1.83 3.13 ±2.04 2.62 ±1.28 NH4

+ 0.32 ±0.15 0.65 ±0.20 0.40 ±0.21 0.35 ±0.26 NO3

- 3.1 ±1.57 22.8 ±1.60 5.1 ±1.42 4.2 ±1.5 PO4

3- 0.7 ±0.47 0.35 ±0.28 0.65 ±0.13 0.57 ±0.09 Cl- 35.0 ±8.08 137.7 ±7.8 39.2 ±10.9 35.5 ±4.8 Ca2+

mg dm-3

76.9 ±20.1 95.2 ±12.9 85.6 ±5.9 81.6 ±11.3


www.oandhs.org

67

They were represented by Oligochaeta and Erpobdella octoculata, and comprised about 35% of all macroinvertebrates found at the site (Fig. 2). Chironomidae was the most numerous family among the insect larvae (about 70%) (Fig. 3). At the site located about 5 km downstream of the discharge canal, Annelida comprised about 10% of all macroinvertebrates (Fig. 2).

Fig. 2. The percentage of different groups of macrofauna in the Krzna River near Międzyrzec Podlaski.

Fig. 3. The percentage of insects and their larvae of different groups of macrofauna in the Krzna River near Międzyrzec Podlaski.



68

Ephemeroptera and Trichoptera were quite numerous (60% of all insects and their larvae found at the site) (Fig. 3). The following numbers of macroinvertebrate families at each sampling site of the Krzna River were noted: site 1 – 26 families, site 2 – 18 families, site 3 – 22 families. The number of Oligochaeta varied between different sites (Table 2). Macroinvertebrate families found at the sampling sites were used to calculate the values of the BMWP-PL biotic index. Mean values of the index for each site located at the Krzna were: 78, 48 and 62 points.

DISCUSSION

Taxonomic composition of macroinvertebrates in rivers depends on many factors, e.g. the purity of water (Cao et al. 1996, Fleituch et al. 2002, Thiėbaut et al. 2006). The discharge of wastewater from the sewage treatment plant in Międzyrzec Podlaski into the Krzna River has an influence on the diversity of the river macroinvertebrates. It lowers the number of macroinvertebrate families and decreases the density of ephemeropteran and trichopteran larvae characteristic of pure and moderately polluted waters (Fig. 3) (Hellawell 1986, Thiėbaut 2006). Sewage input results also in massive appearance of taxa typical of polluted waters, such as Oligochaeta, Erpobdellidae (Fig. 2) and dipteran larvae represented by Chironomidae (Turoboyski 1979).

Hellawell (1986) and Fleituch et al. (2002) pointed out that Ephemeroptera and Trichoptera do not appear in very polluted waters. In the Krzna River 2 families of Ephemeroptera: Ephemeridae and Caenidae, and 2 families of Trichoptera: Limnephilidae and Hydropsychidae were found at the site below the point of wastewater discharge. However, their number was smaller in comparison with the numbers noted at the two other sites. Four families of Trichoptera and 3 families of Ephemeroptera were found at both sites 1 and 3.

The discharge of wastewater also influences the values of the BMWP-PL biotic index. The Ephemeroptera, Plecotera and Trichoptera larvae receive a high number of scores in the BMWP-PL biotic index, adopted for the biological assessment of Polish rivers. Plecoptera were not found at the Krzna sampling sites, while the small number of Ephemeroptera and Trichoptera families at site 2 lowers the value of the BMWP-PL index.

The results show that the discharge of sewage from the treatment plant influences biological indices of water quality to a greater degree than the chemical ones. Chemical indices: phosphate ions at sites 1 and 3, BOD5 and PO4

3- at site 2, electrolytic conductivity and BOD5, allowed for the classification of the Krzna water at all sampling sites and the wastewater in the canal as 3rd quality class. According to the values of the BMWP-Pl index, the Krzna River water was scored the 2nd quality class at site 1, and the 3rd quality class at sites 2


www.oandhs.org

69

Table 2 Taxonomic composition and mean density (number of individuals m-2) of macroinvertebrates in the Krzna River near Międzyrzec Podlaski

Sites Taxa 1 2 3

Oligochaeta 2.5 89.5 3.25 Hirudinea Erpobdellidae 5.25 10.25 5.75 Glossiphoniidae 0.75 0 1.25 Piscicolidae 0.25 0 0.25 Crustacea Gammaridae 60,5 57.25 76.25 Asellidae 12.25 9.0 7.5 Cambaridae 1.25 0 0 Mollusca Bithyniidae 4.25 1.25 2.25 Lymnaeidae 0.25 1.25 1.0 Planorbidae 1.25 0 0.25 Valvatidae 1.75 1.0 1.0 Viviparidae 0 0 0 Sphaeriidae 3.0 4.5 0.5 Unionidae 1.0 0 0 Ephemeroptera Ephemeridae 7.75 0.5 5.5 Caenidae 18.75 15.25 21.25 Baetidae 1.5 0 0.5 Trichoptera Limnephilidae 7.75 1.75 1.5 Phryganeidae 0.5 0 0 Hydroptilidae 0 0 0.25 Hydropsychidae 3.75 0.5 0.75 Polycetropodidae 0 0 0.25 Odonata Calopterygidae 6.5 3.25 3.25 Platycnemididae 0.5 0.5 0 Coleoptera Dytiscidae 1.5 0.75 0 Haliplidae 0.25 0 0 Gyrinidae 1.0 0 1.75 Donaciidae 0 0.5 0 Heteroptera Aphelocheiridae 0 0 0 Gerridae 1.25 0.75 0 Nepidae 0 0 0.5 Megaloptera Sialidae 0 6.25 7.0 Diptera Chironomidae 7.5 72.5 8.75 Simuliidae 7.75 0 0



70

and 3 (Ordinance 2004). However, about 5 km below the outlet of wastewater from the sewage treatment plant the quality of the Krzna River water greatly improves what is reflected by higher value of the BMWP-PL index at the site. Chemical analysis reflects water quality at the time of sampling. Biological indices serve as a measure integrating the environmental impact over a long period of time.

The studies show insignificant influence of the sewage treatment plant in Międzyrzec Podlaski on the quality of the Krzna River water. The quality of the Krzna water 5 km downstream of the discharge point is similar to the quality of the river water flowing upstream of the discharge point.

CONCLUSION

The influx of wastewater from the sewage treatment plant in Międzyrzec Podlaski lowers the quality of the Krzna River water insignificantly. However, 5 km downstream of the discharge canal the water is of much better quality. It is indicated by the results of measurements of selected chemical and biological parameters of water.

REFERENCES

Cao Y., Bark A.W., Williams W.P., 1996, Measuring the responses of macroinvertebrate communities to water pollution: a comparison of multivariate approaches, biotic and diversity indices. Hydrobiologia, 341: 1-19

Fleituch T., Soszka H., Kudelska D., Kownacki A., 2002, Macroinvertebrates as indicators of water quality rivers: a scientific basis for Polish standard method. Arch. Hydrobiol. Suppl. 141(3-4): 225-39

Directive 2000/60/EC of the European Parliament and of the Council of 23 Oct. 2000 establishing a framework for Community action in the field of water policy, OJEC L 327/1 of 22. 12. 2000.

Hellawell J.M., 1986, Biological indicators of freshwater pollution and environmental management. Applied Science Publishers, London, pp. 546

Kondracki J., 1998, Regional geography of Poland, PWN, Warszawa, pp. 441, [Geografia regionalna Polski] (in Polish)

Kornijow R., Lachowska G., 2002, Effect of treated sewage on benthic invertebrate communities in the Upland Bystrzyca Lubelska river (Eastern Poland, [in]: Kownacki, A., Soszka H., Fleituch T., Kudelska D. [eds]: River biomonitoring and benthic invertebrate communities, (Monograph). Warszawa – Kraków, Inst. Env. Protection – Karol Starmach Inst. Freshwater Biol. Polish Acad. Sci., 45-52

Kownacki A., Fleituch T., Dumnicka E., 2002, The effect of treated wastes on benthic invertebrate communities in the mountain zone of the Dunajec River (southern Poland), [in]: Kownacki, A., Soszka H., Fleituch T., Kudelska D. [eds]: River biomonitoring and benthic invertebrate communities, (Monograph). Warszawa – Kraków, Inst. Env. Protection – Karol Starmach Inst. Freshwater Biol. Polish Acad. Sci., 29-43

Kownacki A., Soszka H., Kudelska D., Fleituch T., 2004, Bioassessment of Polish river based on macroinvertebrate, Proceedings of the 11th Magdeburg Seminar on Waters in Central and Eastern


www.oandhs.org

71

Europe: Assessment, Protection Management, Leipzig 18-22.10. 2004 Geller W. et al. (ed.) - UFZ Leipzig-Halle, 250-51

Ordinance of the Minister of Environment Protection of 11 Feb. 2004 concerning the classification which is used to present surface and underground waters state, and the ways of monitoring, interpreting the results and presenting the waters state, DZ.U. Nr 32, poz. 283 and 284: 1729-42, [Rozporządzenie Ministra Środowiska z dnia 11 lutego 2004 roku w sprawie klasyfikacji dla prezentowania stanu wód powierzchniowych i podziemnych, sposobu prowadzenia monitoringu oraz sposobu interpretacji wyników i prezentacji stanu tych wód] (in Polish)

Stańczykowska A., Korycińska M., Królak E., 2002, Effect of treated sewage on benthic invertebrate communities in the lowland Liwiec River (central Poland), [in]: Kownacki, A., Soszka H., Fleituch T., Kudelska D. [eds]: River biomonitoring and benthic invertebrate communities, (Monograph). Warszawa – Kraków, Inst. Env. Protection – Karol Starmach Inst. Freshwater Biol. Polish Acad. Sci., 53-62

Thiėbaut G., Tixier G., Guěrold F., Muller S., 2006, Comparison of different biological indices for the assessment of river quality: application to the upper river Moselle (France). Hydrobiologia, 570: 159-64

Turoboyski L., 1979, Technical hydrobiology, PWN, Warszawa, pp. 443, [Hydrobiologia techniczna] (in Polish)




(73-79) 2007



The role of fish ponds as important habitats for water mites (Hydrachnidia, Acari)

Robert Stryjecki1

University of Agriculture, Department of Zoology ul. Akademicka 13, 20-950 Lublin, Poland

Key words: similarity of faunas, donor habitats, habitat diversity, biodiversity hot spots

Abstract

Fifty-five species of water mites (Acari, Hydrachnidia) were found in four fish ponds located in the Lublin region. Species of the genera Piona, Arrenurus and Limnesia were dominant. Faunal similarity between the ponds was low, from 4.0% to 21.4%. This indicates that these ponds are highly individualised in terms of the faunas inhabiting them. Species diversity of Hydrachnidia in the ponds ranged from 1.53 to 3.78. In certain areas fish ponds can be regarded as biodiversity hot spots.

Fish ponds play an important biocenotic role in standing water systems, especially in areas with few natural standing water bodies.



July 05, 2007 November 16, 2007

R. Stryjecki


74

INTRODUCTION

Man’s influence on the environment, including aquatic ecosystems, is usually negative. Nevertheless, certain aspects of anthropogenic transformation of the environment should be regarded as positive. The creation of artificial water bodies is an example of such positive influence. These water bodies increase landscape and habitat diversity and, consequently, the biological diversity of the areas in which they are created.

Fish-breeding ponds are one type of artificial water bodies. The world literature is lacking in studies on the water mite fauna (Acari, Hydrachnidia) of these water bodies. Polish studies on this topic include Bazan (1962), Narloch (1965), Biesiadka and Kowalik (1980), Kowalik (1980) and Stryjecki (2004a, 2006).

The aim of this paper is to draw attention to the role of fish ponds as water mite habitats, with particular emphasis on the influence of these ponds on Hydrachnidia species diversity in the selected areas.

STUDY SITES AND METHODS

Four fish ponds in the Lublin region were studied: A - Momoty Duże. A eutrophic carp pond with an area of about 20 ha, currently

used for fish farming. The bottom was hard and sandy near the shore and muddy in the centre. Water-column depth at the site of sample collection was up to 1.2 m. The vegetation near the shore consisted mainly of Phalaris arundinacea, Poa palustris, Carex gracilis, and Typha angustifolia. The contribution of Schoenoplect was small, and Eleocharis palustris was observed only in places. Potamogeton lucens grew in the central part of the pond.

B - Momoty Małe. A eutrophic carp pond with an area of about 3 ha, currently used for fish farming. The shores were overgrown with flooded grasses and sedges. The bottom was muddy. Water-column depth at the site of sample collection was up to 1.1 m. Phragmites australis and Typha angustifola grew near the shores. In the central part of the pond Potamogeton lucens was abundant.

C - Stujło. A shallow pond (about 0.6 m in depth), overgrown with vegetation, with an area of about 2 ha. The bottom was muddy; near the shores it was covered with fallen alder leaves. Stratiotes aloides, Nymphaea alba and Potamogeton lucens were abundant. The pond was not used for fish farming during the period when samples were taken.

D - Dziki. A eutrophic pond with an area of about 3 ha. The bottom was hard and sandy near the shore and muddy in the centre. Water-column depth at

The role of fish ponds as important habitats for water mites

www.oandhs.org

75

the site of sample collection was up to 1.3 m. Flooded grasses and Phragmites australis grew near the shore. Further from the shore Elodea canadensis, Stratiotes aloides and Potamogeton lucens were noted. The pond was not used for fish farming during the period when samples were taken. Ponds A and B are situated in Lasy Janowskie Landscape Park (eastern

Poland); ponds C and D are located in Poleski National Park (eastern Poland). Ponds A and B were studied in 1996 and 1997. Semiquantitative samples were taken monthly from March to November with a hand net and a dredge. The samples were taken from ponds C and D in 2006, once a month from June to September, using a hand net and a dredge.

Table 1 shows the number of samples taken from each pond, average sample size and standard deviation. Chao's estimator was used to estimate the potential number of species in each pond. Species diversity was calculated using the Shannon-Wiener Index (base 2 logarithm). Only adults were considered in determining domination structure.


In the four ponds studied, 2371 water mite specimens (1729 adults and 642 deutonymphs) belonging to 55 species were caught. Table 1 shows the number of specimens and species caught in each of the ponds. A detailed list of species is available from the author.

The lower average sample size in pond C and the very low average sample size in pond D in comparison with ponds A and B (Tab. 1) indicate that ponds C

Table 1

Number of specimens, number of species, number of samples, average sample size, standard deviation, estimated number of species and Shannon-Wiener Index values of the ponds studied

Ponds A B C D Total Total specimens 1107 1106 149 9 2371 Total species 35 31 21 3 55 Number of samples 29 30 8 8 Average sample size 38.2 36.8 18.6 1.1 Standard deviation 38.8 33.6 12.3 1.3 Estimated number of species 57 44 28 4 Shannon-Wiener Index 3.78 3.65 3.16 1.53

R. Stryjecki


76

and D actually contain fewer water mites, and not merely that fewer samples were taken from these two ponds. The significantly lower estimated number of species in ponds C and D compared to ponds A and B (Tab. 1) indicate that the smaller number of species noted in pond C (21) and the very small number of species found in pond D (only 3) reflect the actual biocenotic state of these ponds and not merely the smaller amount of material collected.

In the ponds studied (sites A - D), and in three other fish ponds of the Lublin region - Imielty Ług (Stryjecki 2004a), and the two Echo ponds (Stryjecki 2006) - a total of 75 water mite species have been found. These constitute about 55% of the species found in standing waters of south-eastern Poland (lakes of varying trophic state, small permanent water bodies, vernal pools, peat bog pools, ox-bow lakes). Approximately 135 water mite species from 17 families are recorded from south-eastern Poland (Kowalik 1984), and representatives of 16 families have been found in fish ponds. These data suggest that fish ponds play a significant role in the surface water system, constituting an important habitat for water mites typical of standing water.

Dominants (>5% total abundance of adults) in pond A were Arrenurus crassicaudatus (19.9%), Piona pusilla (13.9%), Limnesia maculata (12.6%), L. undulata (12.6%), Forelia brevipes (7.7%) and Piona variabilis (6.9%). Dominants in pond B were Limnesia maculata (24.1%), L. undulata (17.4%), Neumania limosa (9.1%), Piona variabilis (8.3%), Arrenurus crassicaudatus (6.4%), Piona pusilla (5.4%) and Unionicola crassipes (5.2%). Dominants in pond C were Limnochares aquatica (46.8%), Hydrodroma despiciens (12.7%), Hydryphantes dispar (6.3%) and Limnesia fulgida (5.5%). No dominants were distinguished in pond D, as only 9 specimens and 3 species were collected at this site: Limnesia undulata (4 specimens), Oxus ovalis (3 specimens) and Arrenurus tubulator (2 specimens).

The dominance of species of the genera Piona, Arrenurus and Limnesia is typical of standing water bodies, both natural and artificial (Kowalik 1984; Kowalik, Stryjecki 1999; Stryjecki 2004a, 2006). The dominance structure at site C was an exception to this rule. The Stujło pond is in an advanced stage of succession: it has become very shallow, with highly abundant aquatic vegetation. Moreover, it is surrounded by small permanent and astatic water bodies and by peat bog pools. Due to these factors, this pond has a different dominance structure than the others.

Low faunal similarity was noted between the ponds studied (Tab. 2). The greatest similarity was found between Momoty Duże (site A) and Momoty Małe (site B) - 21.4%. The two ponds, located a short distance apart (2 km), are both eutrophic, and their similar habitat conditions contribute to the shaping of similar Hydrachnidia fauna. The lowest faunal similarity - only 4.0% - was


www.oandhs.org

77

between Stujło (site C) and Dziki (site D), both located in Poleski National Park.

New fish ponds differ little from each other. They can be generally described as shallow ponds surrounded by a dike. With time, however, the ponds evolve in different directions. Factors such as when the ponds were created, their size, anthropogenic influences, natural processes and stage of succession all can cause ponds to differentiate over time. Different habitat conditions developing over dozens or even hundreds of years contribute to considerable variation of Hydrachnidia populations between ponds. The low similarity of faunas in the ponds studied indicates that they are heterogeneous habitats. These water bodies are highly individualised, both in terms of habitat characteristics and in terms of the Hydrachnidia populations inhabiting them.

The highest species diversity of water mite fauna was found at site A (the Shannon-Wiener index was 3.78). The lowest species diversity was noted at site D - only 1.53. At sites B and C the Shannon-Wiener index values were moderate (Tab. 1).

It is interesting to compare species diversity in the fish ponds of Lasy Janowskie Landscape Park with its other standing water bodies. In the ponds Momoty Duże (site A), Momoty Małe (site B) and Imielty Ług (Stryjecki 2004a) species diversity ranged from 3.65 to 4.03 and it was higher than in the small astatic pools and peat bog pools (Stryjecki 2004b, c). This indicates that in certain areas fish ponds are biodiversity hot spots.

The number of species and specimens caught in the fish ponds has also been considerably higher than in the other water bodies. In all types of standing water in Lasy Janowskie Landscape Park, a total of 89 water mite species have been found, of which 57 species were caught in fish ponds: Momoty Duże (site A), Momoty Małe (site B) and Imielty Ług (Stryjecki 2004a). As many as 24 were found only in these ponds. These data suggest that fish ponds are not only a substitute habitat for water mites, but may be considered a primary habitat for many species, and can thus be regarded as donor habitats in relation to other

Table 2 Similarity (in %) of faunas at the species level in the ponds studied (the Jaccard formula was used to estimate similarity of faunas)

Ponds A B C D A X B 21.4 X C 13.8 11.8 X D 7.3 5.5 4.0 X

R. Stryjecki


78

standing water bodies. They also can be refuges for water mite species typical of other types of standing water, as water is present in them during the entire vegetation season. Species inhabiting fish ponds can spread to other water bodies and colonise them.

Fish pond complexes are often characterized by high habitat diversity (the ponds differ in size and depth, while feeder channels and drainage channels create varying water flow conditions). There may occur a mosaic of habitats not found in natural hydrological configurations. High habitat diversity in pond complexes translates into high biological diversity. In addition to stagnobiontic species, flowing water species are found as well: rheobionts, rheophiles, crenobionts and crenophiles (Stryjecki 2006). In the ponds selected for this study, two water mite species were caught - Oxus angustipositus and Hygrobates calliger - which had not been noted in any standing waters of the Lublin region. Studies of other fish ponds have also found species not previously noted in standing waters of south-eastern Poland (Stryjecki 2004a, 2006).

CONCLUSIONS

1. Fish ponds are an important habitat for water mites. They play an important biocenotic role in the standing water system of the Lublin region.

2. Fish ponds are not only recipient habitats for water mites typical of standing water. They can be regarded as donor habitats whose fauna spreads to other types of water bodies.

3. Fish ponds are heterogeneous habitats with high diversity. Individual ponds have significantly different Hydrachnidia faunas.

4. The presence of fish ponds in a given area increases the area’s water mite species diversity. Due to the high species diversity noted in some of the ponds, they can be regarded as biodiversity hot spots.

REFERENCES

Bazan H., 1962, The water-mites (Hydracarina) of the Łódź Upland, Fragm. faun., 9: 255-273, (in Polish with Engl. summ.)

Biesiadka E., Kowalik W., 1980, Water mites (Hydracarina) of the Western Bieszczady Mountains. 1. Stagnant waters, Acta hydrobiol., 22: 279-298

Kowalik W., 1980, Water Mites (Hydracarina) of Astatic Waters of the Lublin Region, Ann. UMCS, C, 35: 343-364, (in Polish with Engl. summ.)

Kowalik W., 1984, Faunistic-ecological studies of water-mites (Hydrachnellae) in South-eastern Poland, Rozprawy Naukowe AR w Lublinie, 83: 1-67, (in Polish with Engl. summ.)

Kowalik W., Stryjecki R., 1999, Changes in water mite (Hydracarina) fauna of protected water bodies in Polesie Lubelskie caused by anthropopression [in:] Problems with active protection of aquatic and peat bog ecosystems in Polish national parks, Radwan S.,


www.oandhs.org

79

Kornijów R. (eds.), Lublin, Wydawnictwo UMCS: 211-218, (in Polish with Engl. summ.) Narloch L., 1965, Water-mites (Hydracarina) in one of the fish ponds in Mydlniki near Kraków,

Zesz. nauk. Uniw. jegiellońsk., Prace Zool., 9: 61-67, (in Polish with Engl. summ.) Stryjecki R., 2004a, Water Mites (Acari, Hydrachnidia) of Imielty Ług Reserve, Teka Kom. Ochr.

Kszt. Środ. Przyr., I, 220-225 Stryjecki R., 2004b, Water mites (Acari, Hydrachnidia) of small astatic pools of the Lasy

Janowskie Landscape Park (Southeast Poland) [in:] Acarine Biodiversity in the Natural and Human Sphere, Eds. Weigmann, G., Alberti, G., Wohltmnn, A., and Ragusa S., Phytophaga, XIV (2004): 329-336

Stryjecki R., 2004c, Water mites (Acari, Hydrachnidia) of peat bog pools of the Lasy Janowskie Landscape Park (Southeast Poland) [in:] Acarine Biodiversity in the Natural and Human Sphere, Eds. Weigmann, G., Alberti, G., Wohltmnn, A., and Ragusa S., Phytophaga, XIV (2004): 337-343

Stryjecki R., 2006, Water mites (Acari, Hydrachnidia) of the Echo ponds in the Roztoczański National Park before hydrotechnical restructuring, Acta Agrophysica 7(2): 487-493




(81-96) 2007



Response of riverine benthofauna associated with gravel-pebble bottom to impoundment – interhabitat comparison

Mariusz Tszydel1, Maria Grzybkowska, Michał Kurzawski, Nina Kalisiak

Department of Ecology & Vertebrate Zoology, University of Łódź ul. Banacha 12/16, 90-237 Łódź, Poland

Key words: lowland rivers, dam reservoirs, functional feeding groups, Hydropsyche

Abstract

Variables that have a great impact on riverine macrozoobenthos, like current velocity, discharge, water depth, substrate inorganic composition and food resources were measured downstream of a dam reservoir in three low order lowland streams, over an annual cycle. At the gravel-pebble habitat of each stream site, Chironomidae (which were composed of all their functional feeding groups) dominated in terms of absolute and relative abundance while Oligochaeta (gathering collectors) constituted about 20% of the whole fauna. Only for predators (mainly Tanypodinae, Chironomidae) a similar percentage (about 10% of the total benthic density) was recorded at each site.

A wide spectrum of suitable areas for macroinvertebrates that have different modes of life was recorded in the Mrożyca River, where a great variability of discharge together with large amount of benthic particulate organic matter occurred. In turn, in the Bzura River a large number of gathering collectors might testify to a prevalence of low-flow and high-retention area. The



July 05, 2007 November 07, 2007

M. Tszydel, M. Grzybkowska, M. Kurzawski, N. Kalisiak


82

highest density of zoobenthos was recorded in the Mroga River, in which macroinvertebrates were represented by three groups of almost equal density: gathering and filtering collectors and scrapers. Such composition of functional feeding groups suggests a high-flow and low-retention habitat.

INTRODUCTION

Dam construction appears to have had a greater impact upon the whole aquatic riverine life than any other human activity (Ward and Stanford 1980, Petts 1984, Armitage 1987, Allan 1998, Penczak and Kruk 2005, Penczak et al. 2006, Dukowska et al. 2007). Two primary physical effects of dams that are produced downstream of them are alternations of natural water temperature (it becomes more constant) and flow regimes (they usually deviate from natural conditions). The long-term and diverse intensity changes in the discharge regime may also result in an increase in the heterogeneity of environmental conditions (mosaic downstream site). Such diversification of riverine bottom substrate enables a greater number of co-occurring species of zoobenthos to exist and contributes to lotic invertebrate patchiness (Minshall and Robinson 1998, Lake 2000, Matthaei and Townsend 2000). One of the habitat types that may appear as an effect of high flow fluctuations is a gravel-pebble one.

Among abiotic and biotic factors local inorganic substratum composition together with current velocity, water depth and food availability are known to influence most strongly the microdistribution of lotic macroinvertebrates (Tolkamp 1982, Cummins and Lauff 1969, Minshall and Robinson 1998, Robinson and Minshall 1998, Ciutti et al. 2004, Dukowska et al. 2007). One of the most productive habitats in the rivers is gravel-pebble bottom (Parker and Voshell 1983, Lindegaard 1989, Grzybkowska and Witczak 1990). This kind of habitat tends to trap more fine particulate matter than larger mineral substrata and it offers surfaces for attachment on which it is easy to forage and/or construct larval cases, and to develop biofilm (periphyton). The gravel-pebble bottom may also be considered to be important refuges from predators and provide a heterogeneous substrate enabling numerous macroinvertebrates to co-exist; thus it may be colonized by a high number of macroinvertebrates (Bournaud et al. 1998, Heino et al. 2004).

The main objective of this study was to examine the scale of variability in the taxonomic and functional composition of macroinvertebrate communities in anthropogenically disturbed (by damming) three low order lowland streams, with a special emphasis on benthofauna dwelling of the gravel-pebble habitat. This kind of inorganic substrate heterogeneity is untypical for natural lowland rivers in central Poland and there can be no doubt that it appeared as an effect of flow regime downstream of the reservoir.

Benthofauna associated with riverine gravel-pebble bottom

www.oandhs.org

83

THE STUDY AREA

The small lowland Bzura River is a part of the Vistula drainage basin. The river arises at 235 m a.s.l., and is 166 km long. Its catchment area is 7787.5 km2 and the slope is 2.4‰ in the upper course. The dam reservoir is located 2.6 km from the river’s sources in a first order stream section (Fig. 1). This reservoir, called „Arturówek Dolny”, has an area of 3.05 ha and was constructed in 1963, mainly for the recreation of Łódź citizens.

Fig. 1. The study area with marked sampling sites: BZA (the Bzura River), MRA (the Mroga River) and MCA (the Mrożyca River). The geographical coordinates of each site are given in balloons.



84

The sampling site in the first order stream section (BZA) was located 150 m below the dam reservoir, like our other studied sites described below. The other characteristics of this site are given in Table 1. The Bzura River flows through the forest with the domination of Alnus glutinosa (L.) Gaertn., Fraxinus L. and Salix alba L.

Table 1

Mean values ( x ) and ranges (R) of selected variables at the investigated sites of the streams: Bzura (BZA), Mroga (MRA) and Mrożyca (MCA) over an annual cycle; benthic fine (BFPOM) and coarse particulate organic matter (BCPOM) and transported (TPOM) particulate organic matter, SI - Substrate Inorganic Index

variables

sites BZA MRA MCA

x 0.10 0.28 0.22 depth [m] R 0.08-0.14 0.19-0.55 0.15-0.32

x 0.04 0.16 0.07 current velocity [m s-1] R 0.02-0.06 0.12-0.21 0.03-0.12

x 0.003 0.082 0.158 discharge [m3 s-1] R 0.000-0.005 0.063-0.104 0.068-0.279

x 15.3 18.0 15.9 SI [mm] R 10.5-20.8 12.8-24.7 9.7-20.4

x 61.8 14.6 72.3 BFPOM [g m-2] R 12.3-128.4 3.1-42.1 22.5-139.8

x 5.4 2.9 11.2 BCPOM [g m-2] R 0.03-11.4 0.4-8.7 3.4-34.0

x 1.55 0.13 0.10 TFPOM [g m-3] R 0.04-0.27 0.02-0.38 0.01-0.27

x 11.4 10.9 10.2 water temp. [°C] R -0.1-23.7 2.1-20.6 0.0-20.5

x 7.3 6.0 5.7 oxygen [mg dm-3] R 3.2-8.4 4.2-8.7 3.7-8.5

x 7.3 7.7 7.5 pH R 6.6-8.0 7.4-8.7 6.1-8.0


www.oandhs.org

85

The Mroga River rises at 195 m a.s.l., is 61 km long and empties into the Bzura River. Its catchment area is ca. 531.7 km2 and the slope is 1.8‰. The study area (MRA) was established within a second order stream section, 8 km downstream of the sources (Fig.1). The dam reservoir, called “Bogdanka”, has an area of 4.5 ha and was constructed in the first half of the 60’s of the 20th c., mainly for anglers. Other characteristics of the MRA site are given in Table 1.

The Mroga River flows mostly through meadows and pastures, the riparian trees were characterized mainly by Alnus glutinosa (L.) Gaertn.

The small lowland Mrożyca River is a part of the Vistula drainage basin. The river arises at 195 m a.s.l., and is 27 km long. Its catchment area is 118.9 km2

and the slope 2.4‰. The study area (MCA) was established within a second order stream section, 26 km downstream of the sources. The dam reservoir, called "Stara Piła", has an area of 2.65 ha and was constructed in the second half of the 30’s of the 20th c., mainly in order to supply water to food processing plants and for recreation. The other characteristics of the MCA site are given in Table 1.

The Mrożyca River flows through agricultural land overgrown by meadows and pastures; the riparian trees were characterized mainly by Alnus glutinosa (L.) Gaertn.

The geographical coordinates of each site are given in Fig. 1.


Benthic samples from the gravel-pebble habitats in the Bzura River (BZA - in headwater section), the Mroga River (MRA - the second order section) and the Mrożyca River (MCA - also the second order one) were collected monthly from November 2005 to October 2006. Ten samples were collected with the tubular sampler (25 cm2 in area). The sampler was pushed into sediment to a depth of 15 cm. During the annual sampling cycle depth and current velocity were measured monthly. Additional samples were taken to analyse the composition of particulate inorganic matter according to Cummins (1962). Analysis of size fractions was made on a weight basis. Field data on particle size distribution were transformed into the single substrate index (SI) by summing up the mid-point values of size classes weighted by their percentage cover (Quinn and Hickey 1990). These samples were also used to determine the organic matter content in the bottom sediment. For this purpose a 1 mm sieve was used to separate fractions of particulate organic matter (POM): >1 mm (coarse - CPOM) and <1 mm (fine - FPOM). The size classification of POM followed that used by Petersen et al. (1989). Benthic organic matter (BPOM) was then dried at 60°C for two days, weighed, ashed at 600°C for two hours and reweighed.



86

In order to determine the amounts of transported particulate organic matter (TPOM) in suspension, triplicate water samples were taken in 10 dm3 plastic bags. The samples were filtered through Whatman GF/C glass-fibre filters (1.2 μm). All seston samples were analysed and described as benthic POM.

The macroinvertebrates were hand-sorted in the laboratory, counted and preserved in 10% formaldehyde prepared in river water. Trichopterans were identified to species level where possible; all animals were counted. The data were then used to estimate density for given sampling habitats. The data were log transformed (x+1), when necessary, to satisfy assumption of normality and homogeneity of variance (Elliott 1977). Analysis of variance (one way - ANOVA) was used to examine spatial and temporal variance of benthic and transported organic matter, inorganic substratum, hydraulic parameters, and the other parameters as well as the density of macroinvertebrate taxa. If significant differences were observed among site means, a Tukey multiple comparison test was used to determine which pairs of sites were responsible. Pearson “r” correlation coefficient was used to examine the relationship between the densities of macrobenthic functional groups and environmental variables (StatSoft 2000).

Functional feeding groups (FFGs) of benthos were distinguished on the basis of the primary feeding mechanism of the group, with categories defined as shredders, gathering and filtering collectors, scrapers and predators. This information was derived from Cummins and Klug (1979), Merritt and Cummins (1984), Cummins and Wilzbach (1985), Grzybkowska (1994), Berg (1995) and Nelson (2005).

RESULTS

Environmental variables

Environmental variables of the sites: the Bzura River (BZA), the Mroga River (MRA) and the Mrożyca River are given in Table 1. It appeared that among the sites there were some distinct differences in the values of such variables as discharge, depth, current velocity and the amount of benthic organic matter: its fine (BFPOM) and coarse (BCPOM) fraction. Other parameters, including water quality ones, were much similar among sites (ANOVA, Table 2).

A detailed analysis showed that the differences in riverine depth between BZA and MRA (test Tukey post-hoc p<0.001) as well as between BZA and MCA (p<0.002) were responsible for the result produced by ANOVA. The final result concerning the current velocity over the study period was mainly an effect of differences between MRA and BZA and MCA (p<0.0001) as well as


www.oandhs.org

87

between BZA and MCA (p<0.002). BFPOM also varied among the sites, the significant statistical differences

were recorded between BZA and MRA (post-hoc Tukey test p<0.002), and between MRA and MCA (p<0.0002). For another fraction, BCPOM, the differences were noted between BZA and MCA (p<0.0420) and between MRA and MCA (p<0.003).

An analysis of the seasonal dynamic of discharge in the Bzura River showed the maximum value of this variable in December 2005 and minimum in April 2006; this was caused by emptying of the dam reservoir before winter and its refilling in spring (Fig. 2). Thus, the flow regime of this site deviated from natural conditions. In turn, the sites of the Mroga and the Mrożyca River were established in the same order section but their discharge differed significantly (p<0.001); a greater variability of flow fluctuations was observed in the latter one.

Macrobenthic community

The benthic macroinvertebrate community of the Mroga River may be characterized as a high density, while in the Mrożyca River as a low density one. At the investigated sites two or three groups were prevalent in the macrobenthos: Chironomidae and Oligochaeta in BZA and MCA, whereas

Table 2 A one-way ANOVA was used to determine significant differences between the values of given environmental variables between the streams of Bzura (BZA), Mroga (MRA) and Mrożyca (MCA) over an annual cycle; df = 2; 33 (number of degrees of freedom), F - statistics, p - significance level. Other explanations as in Table 1.

statistics variables F p depth [m] 17.270 0.000 current velocity [m s-1] 102.964 0.000

discharge [m3 s-1] 61.181 0.000

SI [mm] 2.285 0.118

BFPOM [g m-2] 12.870 0.000

BCPOM [g m-2] 7.009 0.003 TFPOM [g m-3] 0.795 0.460 water temp. [oC] 0.066 0.936

oxygen [mg dm-3] 0.079 0.938 pH 1.934 0.161



88

Trichoptera in MRA. Chironomids were very numerous in terms of absolute abundance (over 29000 ind. m-2) in MRA while in terms of relative abundance, but at a lower level, in BZA (over 59.5%). The other group, Oligochaeta, reached about 20% of macrobenthic abundance at each site (Table 3).

Trichoptera also played a key role in benthos, but mainly at MRA. As showed by ANOVA and the post-hoc Tukey test, differences in trichopteran density between BZA and MRA (p<0.0001) as well as between MCA and MRA (p<0.0001) were observed (Table 4). This was an effect of the distribution of Hydropsyche angustipennis and Hydropsyche pellucidula, which were numerically dominant at MRA and they were also present at MCA and BZA, but at a lower abundance. Psychomyia pusilla was recorded only at MCA (Table 3, 4).

In macrobenthic communities of these rivers there were some taxa that appeared only at one and/or at two sites, such as Pisidium and Sphaerium, and insects: Ephemeroptera, Ceratopogonidae and Coleoptera (Table 3, 4).

Fig. 2. Seasonal dynamics of each site discharge of the Bzura River (BZA), the Mroga River (MRA) and the Mrożyca River (MCA).


www.oandhs.org

89

Table 3

Annual density (N - ind. m-2) and percentages of total macroinvertebrates collected in the streams of Bzura (BZA), Mroga (MRA) and Mrożyca (MCA) over an annual cycle. Functional feeding group classification of each benthic taxon is also given: SH – shredders, SC - scrapers, FC – filtering collectors, GC - gathering collectors, P - predators

BZA MRA MCA sitestaxa FFG N % N % N % Oligochaeta GC 6040 25.5 11791 19.2 2589 16.8 Hirudinea P 309 1.3 233 0.4 150 1.0 Pisidium FC 0 0 25 0.1 350 2.3 Sphaerium FC 0 0 8 0.1 642 4.2 Gastropoda SC 718 3.0 92 0.2 742 4.8 Gammaridae GC 355 1.5 8 0.1 875 5.7 Asellus aquaticus GC 9 0.1 0 0 250 1.6 Ephemeroptera

Ephemera GC 9 0.1 0 0 50 0.3 Ephemerella GC 0 0 0 0 392 2.5 Baetis GC 236 1.0 1033 1.7 1042 6.8

Diptera Ceratopogonidae P 391 1.7 0 0 125 0.8 Simuliidae FC 18 0.1 242 0.4 25 0.2 Chironomidae

Tanypodinae P 1091 4.6 8352 13.6 1080 7.0 Orthocladiinae GC 52 0.2 13993 22.8 1843 11.0 Orthocladiinae SC 208 0.9 3471 5.7 636 4.1 Chironomini GC 10497 44.4 4773 7.8 1398 9.1 Chironomini P 416 1.8 - - - - Tanytarsini FC 1767 7.5 651 1.1 763 5.0

Diptera others SH 327 1.4 592 1.0 1108 7.2 Coleoptera P 0 0 8 0.1 358 2.3 Trichoptera

Psychomyia pusilla SC 0 0 0 0 150 1.0 Hydropsyche angustipennis FC 209 0.9 6875 11.2 158 1.0 Hydropsyche modesta FC 9 0.1 8 0.1 0 0 Hydropsyche pellucidula FC 218 0.9 3258 5.3 192 1.3 Hydropsyche sp. juv. FC 118 0.5 5342 8.7 300 2.0

Others 582 2.5 258 0.4 175 1.1 Total 23579 100 61015 100 15393 100



90

Trophic functional groups

The composition of each functional feeding group is given in Table 3. As you can see, differences in functional feeding group abundance among sites were obvious (Fig. 3). The studied sites were numerically dominated by collector-gatherers, animals that feed primarily on deposited fine particulate organic matter. The highest percentage of these macroinvertebrates was recorded at BZA while the lowest one at MRA. This mode of feeding was mainly represented by Oligochaeta and most of Chironomini (Chironomidae).

Table 4 A one-way ANOVA was used to determine significant differences of dominant macroinvertebrates among the streams of Bzura (BZA), Mroga (MRA) and Mrożyca (MCA) over an annual cycle. Other explanations as in Table 2

statistics taxa F p

Oligochaeta 2.700 0.082Hirudinea 3.182 0.054Pisidium 15.447 0.000Sphaerium 33.200 0.000Gastropoda 6.125 0.009Gammaridae 24.384 0.000Asellus aquaticus 3.237 0.000Ephemeroptera

Ephemera 2.600 0.012Ephemerella 3.719 0.011Baetis 9.258 0.009

Diptera Ceratopogonidae 22.291 0.000Simuliidae 2.549 0.093Chironomidae 2.509 0.097

Diptera others 3.342 0.048Coleoptera 1.643 0.000Trichoptera

Psychomyia pusilla 31.970 0.000Hydropsyche angustipennis 17.046 0.000Hydropsyche modesta 0.500 0.611Hydropsyche pellucidula 12.966 0.000Hydropsyche sp. juv. 10.205 0.000

Others 0.100 0.905Total 2.337 0.112


www.oandhs.org

91

In turn, collector-filters are organisms with anatomical structure (setae or fans) or secretions that sieve particulate matter from suspension. At our investigations they were mainly represented by insects: Hydropsyche, Simuliidae and some of Chironomidae (Tanytarsini). The highest percentage of this functional group was estimated in MRA, while the lowest one in BZA.

The Mroga and Mrożyca River sites contained more scrapers (organisms adapted to remove periphyton from rather larger particle size substrate) than the Bzura River; this group was mainly represented by P. pusilla and some of Orthocladiinae (Chironomidae). Shredders constituted only a small part of the whole fauna (mainly crustacean taxa). Predators, i.e. macroinvertebrates that ingest all or part of prey, including mostly Tanypodinae and some other Chironomidae, like carnivorous Cryptochironomus (Chironomini) as well as other insects, constituted close to 10% of the whole fauna (Fig. 3).

The amount of gathering collectors was negatively correlated (Pearson “r” correlation coefficient) with the discharge and current velocity while filtering collectors were positively correlated with these mentioned above hydraulic variables and also with the depth, TPOM, and negatively with BFPOM. We found a significant relationship between scrapers and discharge, BFPOM and

Fig. 3. The percent composition of macroinvertebrate functional feeding groups at each site: BZA (the Bzura River), MRA (the Mroga River) and MCA (the Mrożyca River).



92

BCPOM (positive) while the amount of shredders depended mainly on BCPOM (positive), discharge, and current velocity (negative). The relationships between predators and riverine variables were not significant.

DISCUSSION

Stream regulations such as simplifying the structure of river channel through deepening and straightening as well as impounding altered the trophic structure of macroinvertebrate communities, which is reflected by functional feeding groups (FFGs, Merrit and Cummins 1984). Dams, breaking the upstream-downstream continuum, influence the concentration and transport of POM imported into and exported from the tailwater reach. This impact may be reflected in seasonal changes in size composition of benthic (deposited, BPOM) and transported (TPOM) particulate organic matter, the main food sources for macrobenthos (Grzybkowska and Dukowska 2002). According to Habdija et al. (2003), discharge regime is the most important factor controlling the composition and functional organization of the macrobenthic community inhabiting rather stable, large size mineral substrates like cobbles or pebbles.

Invertebrate FFG percent composition in our study sites (tailwaters) did not show patterns predicted by the River Continuum Concept for the riverine sections of low order (Vannote et al. 1980). This is partly because we analysed only one habitat that was rather untypical for small lowland streams. The rather large particle size mineral substrates found in the Mroga River may explain, firstly, the rather low amounts of BCPOM and BFPOM, and consequently, shredder abundance and, secondly, the presence of microspaces for invertebrates and surfaces for periphyton development, which benefit scrapers. Thus, the relative high abundance of filtering collectors and scrapers in this river suggests a high flow and low-retention habitat. In special environments (downstream of the dam) filtrators like Hydropsychidae may reach relative abundance of 70.3-74.7% of zoobenthos, and of these one species of Hydropsyche as many as 54.7-56.5% (Fiset 1998). In the Mrożyca River the higher proportion of shredders compared with the Mroga River may be explained by higher amounts of BPOM, including its coarse fraction. However, the relative high abundance of scrapers and filtering collectors in this river was also recorded. There can be no doubt that this site represents a wide spectrum of suitable areas for macroinvertebrates with different modes of life. According to Fleituch (2003), differences in feeding behaviour of macroinvertebrates may explain the diverse trait group responses in rivers. Perhaps, the mixed mineral substrates together with the relative high flow fluctuations of the Mrożyca River were responsible for this phenomenon. Accordingly to Miyake et al. (2005), frequent disturbance seems to prevent the most abundant but less mobile taxon


www.oandhs.org

93

from establishing dominance, whereas it seems to enhance the monopoly of the most abundant mobile taxon.

A little different summary composition of invertebrate functional feeding groups was recorded in the Bzura River. Its habitat with a large number of gathering collectors may testify to a prevalence of low-flow and high-retention area. The macrobenthic community of the river was dominated by Chironominae (Chironomini) and Oligochaeta. Emptying of the recreation ponds before winter caused a high discharge downstream of the dam while their refilling in the spring resulted in exposition of the stream bed to air. This kind of river management, which is sometimes applied to recreation ponds, created specific environmental variables in which only some species are able to exist. Recovery to the natural discharge caused the bed sediment to become quickly colonized, mainly by other chironomid species, mostly Micropsectra (Grzybkowska 1994). As it is known, chironomids may reach the substrate within days of rewatering (oviposition, Minshall et. al. 1983). Thus, the disturbance in the Bzura River caused the shift in macroinvertebrate species composition as well as in its density in this downstream habitat (Grzybkowska 1994). The drying up of stream bed followed by its re-filling may be responsible for the low abundance of some taxa, typical of the downstream habitat, such as filtering collectors: net-spinning caddies fly larvae, Hydropsyche and suspension-feeding black fly larvae, Simuliidae (McCullough et al. 1979, Parker and Voshell 1983, Robinson et al. 2003, Tszydel et al. 2003).

Accordingly to RCC (Vannote et al. 1980), predators, a rather diverse group, at the investigated sites fluctuated around 10% of the whole fauna, like in many rivers including lowland and mountain streams (Fleituch 2003, Galas and Dumnicka 2003).

As it is well known, chironomids are common inhabitants of stream communities occupying virtually all functional feeding groups from gathering and filtering collectors to scrapers, shredders and carnivores. Although some chironomid taxa are classified easily into one of the functional feeding groups, others exhibit considerable flexibility in their mode of life; this is often associated with changes in food resources (Berg 1995, Dukowska et al. 1999). Because Chironomidae dominated macrobenthic communities at the investigated streams the obtained functional feeding group composition should be considered with caution.

To sum up, the main conclusion of the present study is that macroinvertebrate communities of the investigated streams are different; this finding confirmed a hypothesis that the benthofauna of headwater sections of streams seems more variable than that in higher order streams, potentially reflecting wider environmental variability of headwater reaches (Heino et al. 2004).



94

ACKNOWLEDGMENTS

This work was partly supported by the grant of University of Łódź No 505/404. The authors are greatly indebted to Ł. Głowacki for help with the English language.

REFERENCES

Allan J.D., 1998, Ekologia wód płynących, PWN, Warszawa, pp.1-451. Armitage P.D., 1987, The classification of tailwater sites receiving residual flows from upland

reservoirs in Great Britain, using macroinvertebrate data [in:] Regulated Streams, Eds. Craig J.F., Kemper J.B., Plenum Publ. Co., pp.131-144.

Berg M.B., 1995, Larval food and feeding behaviour [in:] The Chironomidae. Biology and ecology of non-biting midges, Eds. Armitage P., Cranston P.S., Pinder L.C.V., Chapman & Hall, London, pp. 136-168.

Bournaud M., Tachet H., Berly A., Cellot B., 1998, Importance of microhabitat characteristics in the macrobenthos microdistribution of a large river reach, Annls. Limnol., 34: 83-98.

Ciutti F, Cappelletti C., Monauni C., Siligardi M., 2004, Influence of substrate composition and current velocity on macroinvertebrates in a semi-artificial system, J. Freshwat. Ecol., 19: 455-460.

Cummins K.W., 1962, An evaluation of some techniques for the collection and analysis of benthic samples with special emphasis on lotic waters, Am. Mid. Nat., 67: 477-504.

Cummins K.W., Lauff G.H., 1969, The influence of substrate particle size on the microdistribution of stream macrobenthos, Hydrobiologia, 345: 145-181.

Cummins K.W., Klug M.J., 1979, Feeding ecology of stream invertebrates, Ann. Rev. Ecol. Syst., 10: 147-172.

Cummins K.W., Wilzbach M.A., 1985, Field procedures for analysis of functional feeding groups of stream macroinvertebrates, Appalachian Environmental Laboratory, Univ. Maryland Press, USA, 1611: 1-18.

Dukowska M., Grzybkowska M., Sitkowska M., Żelazna-Wieczorek J., Szeląg-Wasielewska E., 1999, Food resource partitioning between chironomid species associated with submerged vegetation in the Warta River below the dam reservoir, Poland, Acta Hydrobiol. 41 Suppl., 6: 219-229.

Dukowska M., Szczerkowska E., Grzybkowska M., Tszydel M., Penczak T., 2007, Effect of flow manipulations on benthic fauna communities in a lowland river: interhabitat comparison, Pol. J. Ecol., 55: 101-112.

Elliott J.M., 1977, Some methods for the statistical analysis of samples of benthic invertebrates, Freshwat. Biol. Assoc. Sci. Publ., 25: 1-156.

Fiset W., 1998, Response of benthic macroinvertebrate communities downstream of a peaking hydroelectric generation station in Northeastern Ontario, NEST Technical Report TR-036, pp 1-36.

Fleituch T., 2003, Structure and functional organization of benthic invertebrates in a regulated stream, Internat. Rev. Hydrobiol., 88: 332-344.

Galas J., Dumnicka E., 2003, Organic matter dynamics and invertebrate functional groups in a mountain stream in the west Tatra Mountains, Poland, Internat. Rev. Hydrobiol., 88: 362-371.

Grzybkowska M., 1994, Impact of human-induced flow perturbation on the chironomid communities in the first order stream section of the Bzura River (Central Poland) [in:]


www.oandhs.org

95

Chironomids - from genes to ecosystems, Ed. Cranston P., CSIRO Publications, Victoria, Australia, pp. 247-253.

Grzybkowska M., Witczak J., 1990, Distribution and production of Chironomidae (Diptera) in the lower course of the Grabia River (Central Poland), Freshwat. Biol., 24: 519-531.

Grzybkowska M., Dukowska M., 2002, Communities of Chironomidae (Diptera) above and below a reservoir on a lowland river: long-term study, Annals. Zool., 52: 235-247.

Haabdija I., Radanović I., Primc-Habdija B., Matonićkin R., Kućinić M., 2003, River discharge regime as a factor affecting the changes in community and functional feeding group composition of macroinvertebrates on a cobble substrate in the Sava river, Biologia, Bratislava, 58: 217-229.

Heino J., Louhi P., Muotka T., 2004, Identifying the scales of variability in stream macroinvertebrate abundance, functional composition and community structure, Freshwat. Biol., 49: 1230-1239.

Lake P.S., 2000, Disturbance, patchiness, and diversity in streams, J. N. Am. Benthol. Soc., 19: 573-592.

Lindegaard C., 1989, A review of secondary production of zoobenthos in freshwater ecosystems with special reference to Chironomidae (Diptera), Acta Biol. Debr. Oecol. Hung., 3: 231-240.

Matthaei C.D., Townsend C.R., 2000, Long-term effects of local disturbance history on mobile stream invertebrates, Oecologia, 125: 119-126.

McCullough D.A., Minshall G.W., Cushing C.E., 1979, Bioenergetics of lotic filter-feeding insects Simulium spp. (Diptera) and Hydropsyche occidentalis (Trichoptera) and their function in controlling organic transport in streams, Ecology, 3: 585-596.

Merritt R.W., Cummins K.W., 1984, An introduction to the aquatic insects of North America, Kendall/Hunt Publishing Company, Dubuque, Iowa.

Minshall G.W., Petersen R.C., Cummins K.W., Bott J.R., Sedell J.R., Cushing C.E., Vannote R.L., 1983, Interbiome comparison of stream ecosystem dynamics, Ecol. Monog., 53: 1-25.

Minshall G.W., Robinson C.T., 1998, Macroinvertebrate community structure in relation to measures of lotic habitat heterogeneity, Arch. Hydrobiol., 141: 129-151.

Miyake Y., Hiura T., Nakano S., 2005, Effects of frequent streambed disturbance on the diversity invertebrates, Arch. Hydrobiol., 162: 465-480.

Nelson M.S., 2005, Stream Macroinvertebrate Surveys in the Cle Elum and Bumping River Watersheds, Storage Dam Fish Passage Study, Yakima Project, Washington, Technical Series No. PN-YDFP-002, Bureau of Reclamation, Boise, Idaho.

Parker C.R., Voshell J.R., 1983, Production of filter-feeding Trichoptera in an impounded and a free-flowing river, Can. J. Zool., 61: 70-87.

Penczak T., Kruk A., 2005, Patternizing of impoundment impact (1985-2002) on fish assemblages in a lowland river using the Kohonen algorithm, J. Appl. Ichthyol., 21: 169-177.

Penczak T., Kruk A., Grzybkowska M., Dukowska M., 2006, Patterning of impoundment impact on chironomid assemblages and their environment with use of the self-organizing map (SOM), Acta Oecol., 30: 312-321.

Petersen R.C., Cummins K.W., Ward G.M., 1989, Microbial and animal processing of detritus in a woodland stream, Ecol. Monogr., 59: 21-39.

Petts G.E., 1984, Impounded rivers. Perspectives for ecological management, Chichester. Wiley and Sons, 1-326 pp.

Quinn J.M., Hickey C.W., 1990, Magnitude of effects of substrate particle size, recent flooding, and catchment development on benthic invertebrates in New Zealand rivers, N. Z. J. Mar. Freshwat. Res., 24: 387-409.

Robinson C.T., Minshall G.W., 1998, Macroinvertebrate communities, secondary production, and life history patterns in two adjacent streams in Idaho, USA, Arch. Hydrobiol., 142: 257-



96

281. Robinson C.T., Uehlinger U., Monaghan M.T., 2003, Effects of a multi-year experimental flood

regime on macroinvertebrates downstream of a reservoir, Aquat. Sci., 65: 210-222. StatSoft Inc., 2000, Statistica for Windows (Computer program manual, version 5.5), Tulsa. Tolkamp H.H., 1982, Microdistribution of macroinvertebrates in lowland streams, Hydrobiol.

Bull., 16: 133-148. Tszydel M., Szczerkowska E., Grzybkowska M., Dukowska M., 2003, Populational parameters

of trichopterans (Trichoptera) in dominant habitats of a permanently disturbed lowland river, Acta Agrophysica, 88: 585-594.

Vannote R.L., Minshall G.W., Cummins K.W., Sedel J.R., Cushing C.E., 1980, The river continuum concept, Can. J. Fish. Aquat. Sci., 37: 130-137.

Ward J.S., Stanford J.A., 1980, Tailwater biota: ecological response to environmental alternations, Proceedings of the symposium on surface water impoundments ASCE, Minneapolis, Minnesota, pp. 1516-1525.




(97-108) 2007



Size differences between individuals of Nannopus palustris Brady, 1880 (Crustacea, Harpacticoida, Huntemannidae) from

tidal flats on Spitsbergen

Barbara Wojtasik(1),a, Jarosław Kur(2),b

(1)Department of Genetics, University of Gdansk Al. Piłsudskiego 46, 81-378 Gdynia, Poland

(2)Institute of Nature Conservation, Polish Academy of Sciences Al. A. Mickiewicza 33, 31-120 Kraków, Poland

Key words: Nannopus palustris, Harpacticoida, morphological parameters, populations, Spitsbergen

Abstract

The investigation of Copepoda shows differences between morphological characteristics of 2 populations of Nannopus palustris, which inhabit tidal flats of Spitsbergen: Petunia Bay and Nottingham Bay. Ecosystems of tidal flats are utterly different and some morphological differences in body size of Nannopus palustris can be expected. The analysis of three variables was conducted for both studied populations: the length and width of individuals, and the length of the last segment of maxillipeds. The body length of N. palustris from Petunia Bay was statistically meaningful at significance level P<0.05 when compared to the body length of individuals from Nottingham Bay. N. palustris that came flooding into Nottingham Bay belongs to a different population than specimens from Petunia Bay. Moreover, they can be a set of random specimens from more than one population. a e-mail: [email protected] b e-mail: [email protected]


July 05, 2007 November 07, 2007

B. Wojtasik, J. Kur


98

INTRODUCTION

Nannopus palustris (Brady 1880) is a cosmopolitan marine copepod that usually inhabits muddy intertidal sediment (Lang 1936). Abundance and distribution of this species on Spitsbergen (Svalbard) were discussed by many authors (Węsławski & Szymelfenig 1999, Soltwedel et al. 2000, Kotwicki 2002). First studies of the harpacticoids of the Arctic Seas were published by Scott and Scott (1901) and Lang (1936).

As in the case of other marine invertebrates that have wide geographic range, changes of morphotic features can be observed. Three morphotic types of N. palustris have been distinguished (Por 1968, Wells 1971, Coull & Fleeger 1977, Staton et al. 2005). The three morphs differ significantly in width. The differences in morphological characteristics among copepoda populations from Svalbard were not yet discussed in any publications. Morphotic types of N. palustris were described many times but morphometrical differences among individuals that form the above-mentioned populations, however, were not investigated in detail. Differences in body size between two populations of the same species of copepoda were analysed by Elgmork & Halvorsen (1976) and Lock & McLaren (1970). Generally, the influence of temperature and food on the size of marine copepods can be observed (McLaren 1963). Maxilliped length was also positively correlated with environmental factors (Tsotetsi 2006).

Ecosystems of the tidal flats of Petunia Bay and Nottingham Bay are utterly different. This is why some morphological differences in N. palustris body size can be expected.

Our investigation provides evidence that different environmental conditions on tidal flats in question may be the reason for the observed morphological differences. It should be emphasized that the morphological deviations concern the body length only. This paper shows differences between morphological characteristics of 2 populations of N. palustris, which inhabit tidal flats: Petunia Bay and Nottingham Bay.

RESEARCH AREA

The area of Arctic tidal flats is under the influence of waters of both marine and terrestrial origin. The quantity of freshwater that originates in melting glaciers is limited by tide-driven changes in sea level. During high tide, the large area of tidal flats is flooded with seawater whilst during low tide a large internal zone of alluviation is sometimes uncovered. It creates difficult environmental conditions for organisms living in tidal flats. The study area is located on two tidal flats on West Spitsbergen coast: Petunia Bay (Petuniabukta) and Nottingham Bay (Nottinghambukta). The first one is on the

Size differences between individuals of Nannopus palustris

www.oandhs.org

99

northern ending of Billefjorden (Isfjorden), about 100 km from the Greenland Sea. The other one is located on SW coast of Spitsbergen and separated from the Greenland Sea by skiers and Dun Islands.

Post-glacial waters from Hörbye and Ebba glaciers affect the development of the tidal flat of Petunia Bay. Hörbye glacier, the largest in the neighbourhood of Petunia Bay, is a northern ending of the bay. Ebba glacier is located east from Petunia Bay and together with Bertram glacier forms a catchment area from where waters flow into the bay (Karczewski & Rygielski 1989, Choiński 1989). The average annual temperature (the meteorological station in Longyearbyen, 60 km from Petuniabukta) during the years 1961-1990 was 6.5

°C. Annual precipitation was 199 mm. In the eastern coast of Petunia Bay the average mid-summer temperature in 2000 was 7.4°C and in 2001, 7.1°C. In August 2001 the maximum temperature was 18.8°C (Rachlewicz 2003).

Nottingham Bay is a vast, shallow bay. In the active hydrological period the waters from the nearby glacier Werenskiold, the Brattega River and tundra periodical small rivers flow to the bay and contribute to water salinity decrease in the vast Nottinghambukta region. Changeable microhabitat conditions occurring in the active hydrological period (active hydrological period begins in June by spring flood due to snow cover melting in the coastal plains and ends at the beginning of October when glacier ablation and permafrost thawing terminate and rivers are frost-bound to the bottom (Bartoszewski 1998) impose severe restrictions on the organisms inhabiting the bay (Wiśniewska-Wojtasik & Kheireddine 2005). The average annual temperature in the years 1979-2006 (the meteorological station in Polish Polar Station, 20 km from Nottingham Bay) was -4.4°C. The average mid-summer temperature (July and August) in 2000 was 4.5°C and in mid summer 2001, 4.7°C. Maximum temperature observed in Hornsund was 13.5°C (July 2005). The annual precipitation during the years 1979-2006 was 430 mm (Marsz & Styszyńska 2007). Fig. 1 shows the research area.


Sample collection

The samples from Nottingham Bay were collected on 02 of July 2000. The samples from Petunia Bay were collected on 27-29 of July 2002 from different stations on tidal flat (Fig. 1). The samples were collected at the stations of different water salinity and temperature: Nottingham Bay: 0-5.8 PSU, 9.4-11.9°C, Petunia Bay: 0.2-9.3 PSU, 6.6-9.4°C (Table 1). Qualitative samples were collected with a net dipper – 0,042 mm mesh. The samples were preserved in 70% ethanol.

B. Wojtasik, J. Kur


100

Systematic position of Harpacticoida and identification to the species level

were determined according to Lang (1936; 1948) and Bodin (1997).

Data analysis

Some samples were separated under a stereomicroscope in the laboratory (magnification to ×10). After separation and extraction, the organisms were identified and measured under an optical microscope (magnification to ×100). Calibrated lens were used to measure each individual. The values of

Fig. 1. Research area: Spitsbergen, Petunia Bay (Central Spitsbergen), Nottingham Bay (SW Spitsbergen).

Table 1 Temperature and salinity of water above the sediment of Petunia Bay and Nottingham Bay

Petunia Bay Nottingham Bay Station Temperature [°C] Salinity [PSU] Station Temperature [°C] Salinity [PSU]

1 2 3 4 5

6.6-6.7 8.2 7.0 9.4

8.2-8.5

0.2-1.8 0.9-1.4 8.9-9.3 1.6-3.4 1.4-2.6

1 2

10.0-11.4 9.4-11.9

0.0-5.8 2.5-4.7


www.oandhs.org

101

measurements were decoded in micrometers. In preliminary investigations more than 90 copepods were used. Only 43 adult females with the same morphs (Staton et al. 2005) from Petunia Bay and 30 adult females from Nottingham Bay have been chosen. Males were not used for analysis. Three morphological characteristics (the length and width of the body and the length of the last segment of maxillipeds) were measured (Fig. 2).

Mathematical analysis

Data were analysed statistically and computed with the use of statistical hypothesis testing. The hypotheses were computed for the statistical significance of the differences between the two populations. They were also computed for the difference in morphological characteristics of the populations. It is the basis of popular tests for the statistical significance of the difference between the means of two samples and also the basis of tests for confidence intervals for the difference between two means of populations (Table 2). The Z-

Fig. 2. N. palustris: a) the photo of an individual, b) measured body sizes: the length of individuals [l], the width of individuals [w], c) the length of the last segment of maxillipeds [Mxp] (figures of N. palustris after Sars 1903-1911).

B. Wojtasik, J. Kur


102

test analyses samples from general population when the sample size is small, i.e. 30-40 (Łomnicki 1995). The Z score is compared to the table Z value. The table contains the percent of area under the normal curve between the mean and the Z score. This method can be employed to analyse the means from two different populations and to mark the differences among parameters of each population.

One variable analysis was conducted for both studied populations. Three variables: the length of individuals [l], the width of individuals [w] and the length of the last segment of maxillipeds [Mxp] (Fig. 2) were analysed separately for each population. Mean, standard deviation and median were calculated for each variable. Outliers and extremes were also determined. For each variable, differences between populations were tested using Z-test for the difference between two means (Table 1). Scatterplots, versus, plots were analysed for both populations of N. palustris females. Finally, 3D scatterplots and versus were analysed and the data were extrapolated for the female populations of each tidal flat. Comparing 2 or 3 body parameters it is possible to state the differences between populations.


An analysis of one variable (the length of individuals, the width of individuals and the length of the last segment of maxillipeds) for females from

Table 2 List of mathematical results

Population 1 (Petunia Bay) Population 2 (Nottingham Bay)

Length of the last

segment of maxilliped [Mxp]

Length of body [l]

Width of body [w]

Length of the last segment of

maxilliped [Mxp]

Length of body [l]

Width of body [w]

The amount of measure 43 43 43 30 30 30

Mean of the sample [µm] 35.20 595.5 207.99 35.31 620.06 210.31

The standard error SE 0.45 9.19 1.60 0.37 11.32 2.64

The standard deviation SD 2.96 60.24 10.51 2.02 62.00 14.46

The Z-test 0.24 2.67 1.45 The level of

relevance 0.05 to the means

1.96 1.96 1.96


www.oandhs.org

103

two tidal flats was carried out. All calculations were performed for the relevance level 0.05. Generally, the only statistically meaningful difference between populations of N. palustris from Petunia Bay and Nottingham Bay is the body length. This sort of difference was also noted previously in 2 ponds with similar water temperature but different environmental conditions (Elgmork & Halvorsen 1976). The influence of temperature on the size of marine copepods was described by Deewey (1960) and Lock & McLaren (1970). Their experiments confirm the negative, curvilinear response of female size to temperature.

No statistical differences were stated between the width and the length of the last segment of maxilliped. The positive correlations between length and food conditions were noted by Tsotetsi (2006).

The determined factor value is fundamentally higher in the case of specimens from Nottingham Bay but dispersion of value was bigger in the case of Petunia Bay. The received results show the significantly greater value of the parameter. A comparison of regularized range of value for an individual variable is shown in Fig. 3a, b, c. Fig. 4a presents mean values along with standard deviation. Fig. 4b shows the value of median. For all the investigated

a) b)

c)

Fig. 3. Measured body sizes: a) Length of individuals, b) Width of individuals, c) Length of the last segment of maxilliped of individuals from tidal flats: P(F) – females from Petunia Bay, N(F) – females from Nottingham Bay (Statistica v.7.1)

B. Wojtasik, J. Kur


104

variables the average values are higher in the case of Nottingham Bay. Median is slightly different from the mean value despite the significant number of outliers. It shows that the distribution of the investigated values is symmetrical.

In the case of the analysis of two variables (length and width of females), more symmetrical distribution of values can be noted for the population from Petunia Bay (Fig. 5a, b). Moreover, a group of females with similar body width but different body length can be distinguished. In the case of Nottingham Bay, the distribution is less symmetrical. The most numerous group of females with the same body width but different body length is shifted to the right along x-axis comparing to a parallel (the most numerous) group from Petunia Bay.

The 3D scatterplots analysis shows that the variables are more focused in the case of Petunia Bay female population (Fig. 6a, b).

From the obtained results of analysis and - in particular - from the extrapolation of data, distinct differences in both investigated populations can be seen. The differences can result from the geographical position and the prevailing environmental conditions both in Petunia Bay and Nottingham Bay. In Petunia Bay water salinity was 0.2-9.3 PSU and the temperature was 6.6-9.4°C (Wojtasik, Janiszewska, unpublished data). In Nottingham Bay water salinity was 0-5.8 PSU and the temperature was 9.4-11.9°C. Growth of temperature causes a faster development of Copepoda. Concurrently, mature specimens are smaller when temperature is high. Specimens of the same invertebrates species are smaller when salinity is low. In the investigated case

a) b)

Fig. 4. a) Mean values along with standard deviation of three parameters (length, width and length of the last segment of Maxilliped) of N. palustris females from Petuniabukta and Nottinghambukta, b) The value of median of three parameters (length, width and length of the last segment of Maxilliped) of N. palustris females from Petuniabukta and Nottinghambukta (Statistica v.7.1)


www.oandhs.org

105

a) b)

Fig. 5. The analysis of two variables (length and width) of N. palustris females from: a) Petuniabukta, b) Nottinghambukta (Statistica v.7.1). a) b)

c) d)

Fig. 6. The 3D scatterplots analysis of variables (length, width and length of the last segment of Maxilliped) of N. palustris females from a) Petuniabukta, b) Nottinghambukta and the extrapolation of data (length, width and length of the last segment of Maxilliped) of N. palustris females from c) Petuniabukta, d) Nottinghambukta (Statistica v.7.1).

B. Wojtasik, J. Kur


106

the temperature was higher in Nottingham Bay whereas monitored salinity was higher in Petunia Bay. One may make a hypothesis that such parameter diversity could be the cause of nearly symmetrical appearance of both graphs (Fig. 6c, d). In the present phase of investigation on N. palustris it is impossible to state whether the growth of temperature with the simultaneous drop of salinity is the cause that specimens grow faster or the other way round.

There is another possibility: Petunia Bay as the last part of the second biggest fjord on Spitsbergen, Isfjordu (over 100 km) has no direct access to the open waters of Greenland Sea. In connection to this, the population of N. palustris that lives in Petunia Bay has a small chance to contact any new populations. The stations at which N. palustris was found were situated in the inner part of the bay. Some of them were situated in standing waters never reached by all tidal waves from the sea. In view of the lack of earlier data on N. palustris from Petunia Bay, it is impossible to determine for how long this species has been populating this area. A different situation occurs in Nottingham Bay, which is under the direct influence of Greenland Sea. As it results from earlier data (Wiśniewska 2001), in the years 1993-1999 N. palustris was not found in Nottingham Bay. This species appeared in 2000 when the investigated material was sampled (Wojtasik, Staniszewska, unpublished data). It can be assumed that specimens of N. palustris that came flooding into Nottingham Bay belong to a different population than specimens from Petunia Bay. Moreover, they can be a set of random specimens from more than one population.

REFERENCES

Bartoszewski S., 1998, Reżim odpływu rzek Ziemi Wedel Jarlsberga (Spitsbergen). Flow regime of rivers in Wedel Jarlsberg Land (Spitsbergen). Wydawnictwo UMCS, Lublin: 168 (in Polish with English summary)

Bodin P., 1997, Catalogue of the new marine Harpacticoid Copepods. Koninklik Belgisch Institut voor Natuurwetenschappen. Studiedokumenten van Het K. B. I. N. Brussel: pp. 340

Choiński A., 1989, Hydrology of the mouth section of the Ebbavelva and the Petuniabukta, Billefjorden, Central Spitsbergen. Polish Polar Res. 10, 3: 457-64.

Coull B.C., Fleeger J.W., 1977, A new species of Pseudostenhelia and morphological variation in Nannopus palustris (Copepoda, Harpacticoida). Transactions of the American Microscopical Society 96: 332–40

Deewey, G. B., 1960, Relative effects of temperature and food on seasonal variations of length of marine copepods in some eastern American and western European waters. Bull. Bingham Oceanogr. Coll. 17(2) : 55-86

Elgmork K., Halvorsen G., 1976, Body Size of Free-Living Copepods. Oikos, 27, 1: 27-33 Karczewski A., Rygielski W., 1989, The profile of glacial deposits in the Hörbyedalen and an

attempt at their chronostratigraphy, Cenral Spitsbergen. Polish Polar Res. 10, 3: 401-409. Kotwicki L., 2002, Benthic Harpacticoida (Crustacea, Copepoda) from the Svalbard

archipelago. Polish Polar Res. 23, 1: 185–91.


www.oandhs.org

107

Lang K., 1936, Die wahrend der Schwedischen Expedition nach Spitzbergen 1899 eingesammelten harpacticiden. Kungliga Svenska Vetenskapsakademiens Handlingar (4) 3: 1–55 (in German)

Lang K., 1948, Monographie der Harpacticiden. Håkan Ohlssons Boktryckeri, Lund (Sweden): pp1683 (in German)

Lock A. R., McLaren I. A., 1970, The effect of varying and constant temperatures on size of marine Copepods. Limnology and Oceanography. 15, 4, 638-640

Łomnicki A., 1995, Wprowadzenie do statystyki przyrodników (Basic statistics for biologists). PWN Poland: pp. 245 (in Polish)

Marsz A., Styszyńska A., (Eds.), 2007, Klimat rejonu Polskiej Stacji Polarnej w Hornsundzie - stan, zmiany i ich przyczyny. The climate of the Polish Polar Station region, Hornsund – state, changes and their reasons. Wydawnictwo Akademii Morskiej w Gdyni: pp. 376 (in Polish)

McLaren I. A., 1963, Effects of temperature on growth of zooplankton and the adaptive value of vertical migration. J. Fish. Res. Bd. Can. 20: 685-727

Por F.D. 1968. The benthic Copepoda of Lake Tiberias and some inflowing springs. Israel. J. Zoology 17: 31–50

Rachlewicz G. 2003. Warunki meteorologiczne w Zatoce Petunia (Spitsbergen Środkowy) w sezonach letnich 2000 i 2001. Meteorological conditions in Petunia Bay (Central Spitsbergen) during summer seasons 2000 and 2001. Problemy Klimatologii Polarnej 13: 127-138 (in Polish with English summary)

Sars G. O., 1903-1911, An account of the Crustacea of Norway with short descriptions and figures of all the species. Copepoda Harpacticoida. Bergen Museum, Bergen: pp. 368.

Scott T., Scott A., 1901, On some Entomostraca collected in the Arctic Seas in 1898 by William S. Bruce, Annals and Mag. Natural History Series 7, 8: 337–56

Soltwedel T., Mokievsky V., Schewe I., 2000, Benthic activity and biomass on the Yermark Plateau and in adjacent deep-sea regions northwest of Svalbard. Deep Sea Res. I, 47: 1761-85

Staton J.S, Wickliffe L.C., Garlitska L., Villanueva S.M., Coull B.C., 2005, Genetic isolation discovered among previously described sympatric morphs of a meiobenthic copepod, J. Crustacean Biol. 25 (4): 551–57

Tsotetsi A. M., Avenant-Oldewage A, Mashego N. S., 2006, Aspects of the ecology of Lamproglena clariae (Copepoda: Lernaeidae) from The Vaal River System, South Africa. J. Crustacean Biol. 24, 4: 529–536

Wells J. B. J., 1971, The Harpacticoida (Crustacea: Copepoda) of two beaches in south-east India. J. Natural History 5: 507–20

Węsławski J.M., Szymelfenig M,. 1999, Community composition of tidal flats on Spitsbergen. Consequence of disturbance? [in:] Gray J.S. et al. (eds), Biogeochemical Cycling and Sediment Ecology. Kluver Academic Publishers: 185–93

Wiśniewska B., 2001, Perennial fluctuation of Harpacticoida inhabiting Nottinghambukta (South Spitsbergen) with careful consideration for their wintering strategies. Intern. Symp. Functioning of Coastal Ecosystems in Various Geographical Regions, Book of Abstracts, Gdynia: 73-74.

Wiśniewska-Wojtasik B., Kheireddine A., 2005, Zmienność zgrupowań meiobentosu w sezonie hydrologicznym 2001 w zatoce Nottingham, SW Spitsbergen (Changeability of meiobenthic communities in hydrological season 2001, in Nottingham Bay, SW Spitsbergen). Polish Polar Studies, XXXI Sympozjum Polarne, Kielce: 166-80 (in Polish with English summary).




(109-117) 2007



Various reproductive strategies of two species of Oligochaeta:

Limnodrilus hoffmeisteri and Tubifex tubifex

Janusz Żbikowski1

Nicolaus Copernicus University Institute of Ecology and Environment Protection, Department of Hydrobiology

ul. Gagarina 9, 87-100 Toruń, Poland Key words: Oligochaeta, Tubificidae, population size structure, reproductive activity

Abstract

The aim of the present paper was to compare the size structure and seasonal changes in the reproductive activity of two commonly occurring species of Oligochaeta. The research was carried out in a small, shallow, eutrophic, anthropogenic lake. It was found that very young individuals were the most numerous in Tubifex tubifex population, whereas individuals of average size were predominant in Limnodrilus hoffmeisteri population. These differences are probably the consequence of the different reproductive strategy displayed by the two species. Tubifex tubifex individuals were characterized by a greater reproductive potential but a lower survival rate among young individuals. Moreover, individuals capable of reproducing were found throughout the year in the case of Limnodrilus hoffmeisteri, while the reproduction of Tubifex tubifex was limited to certain periods of the year, although it was very intensive. 1 e-mail address: [email protected]


July 05, 2007 November 23, 2007

J. Żbikowski


110

INTRODUCTION

Tubificid oligochaetes were found to comprise a major portion of the benthic macroinvertebrate fauna, especially in the extralittoral zone of water bodies. The most widespread species inhabiting in large numbers different types of water bodies include Tubifex tubifex (Muller 1774) and Limnodrilus hoffmeisteri (Claparede 1862). Because of the very high density, considerable body size reached by these taxa and the beneficial effect on sediment transformation, their role in the functioning of water bodies seems hard to overestimate.

However, the total number and biomass of a population are often insufficient and it is the determination of the exact age and/or size structure that proves to be very helpful in evaluating the physiological state of the individuals (also dependent on environmental conditions), which has a direct influence on reproduction, growth rate, survival rate and migration and considerably facilitates the prediction of possible changes in the abundance of the species being researched (Pasteris et al. 1996, 1999). Moreover, the role of the population in the environment also depends to a certain extent on the proportion of individuals of different ages (Tatrai 1982).

It is generally known that bottom fauna – including Oligochaeta – is a good indicator of the ecological situation in water bodies (Lang & Reymond 1995, Finogenova 1996, Verdonschot 1996, Risnoveanu & Vadineanu 2001). Apart from its taxonomic composition and abundance, the rate at which young individuals appear and their survival rate, and also growth rate, as well as the duration and appearance of the reproductive period provide valuable indirect information about the conditions present in the bottom deposit layer. The reproduction of T. tubifex is also used as an environmental toxicity test (Bailey et al. 1995, Reynoldson et al. 1995).

Taking the above assumptions into consideration, the aim of this paper is to determine the size structure of two species of Oligochaeta – Tubifex tubifex and Limnodrilus hoffmeisteri – which inhabit a small anthropogenic water body near Toruń. These taxa are the only representatives of Oligochaeta in this water body. The data obtained contribute to a fuller characterization of the macrobenthos of this basin, and also provide indirect information on the environmental conditions present in the bottom deposit layer.


The research was conducted in a small (surface area 8 ha) and shallow (av. depth 3 m) anthropogenic water body formed as a result of filling with water a

Various reproductive strategies of two species of Oligochaeta

www.oandhs.org

111

gravel pit created in 1993 during the construction of the Toruń stretch of the A-1 motorway.

The results of physical and chemical tests on the water of the water body (Marcinkowski 1999) and tests on the zooplankton (Przybylak 1998) unequivocally indicate the eutrophic character of the basin under study. Despite the relatively good exposure to wind and the shallow depth, the oxygenation of the over bottom layer of water (2-3 cm above the bottom) was very low in the vegetative season (Żbikowski, unpublished data). Since 1996, the water body has been leased by the Toruń Angling Society and is therefore well stocked with fish of different species, including benthivorous, which might suggest considerable pressure on the bottom fauna.

The research station was located in the central part of the water body, which is characterized by having the most representative bottom fauna of the whole basin (Żbikowski, unpublished data). The bottom is sandy with a small amount of organic matter (0.8%), without macrophytes, depth about 3 m. The research was carried out from January 2001 to January 2002. During this time, 11 samples were taken on the following dates: 16 January, 9 April, 16 and 25 May, 2 and 20 June, 5 and 20 July, 14 September, 15 October in 2001 and 8 January in 2002. The samples were collected with an Ekman-Birge mud sampler with a catching area of 225 cm2. The contents of the Ekman were rinsed in a sieve with a 0.2 × 0.2 mm mesh.

In the studied water body Oligochaeta were represented by only two species: Limnodrilus hoffmeisteri and Tubifex tubifex, so differentiating between even sexually immature individuals was not a great problem because only the latter have hairy bristles in spinal fascicles.

The size structure of the species of Oligochaeta being studied was determined on the basis of the width of the 8th segment of the body, measured using a microscope equipped with a measuring eyepiece. The reason for taking this parameter is connected with the fact that Oligochaeta often lose the rear part of the body, which protrudes from the surface of the deposit, due to pressure from predators (Wiśniewski 1978), which makes it impossible to use body length in determining population size structure. Another problem is the spirally twisted body of Oligochaeta (as a result of fixing), which also makes it impossible in practice to measure the length exactly. In turn, the width of the 8th segment of the body – like the length – correlates to a considerable degree with biomass (Dżenderezjan and Unanjan 1987), and is, moreover, very easy to measure.

The following size classes were distinguished:

J. Żbikowski


112

Class Width of 8th segment (mm) Class Width of 8th segment (mm) II 0.11 – 0.19 VI 0.50 – 0.59 III 0.20 – 0.29 VII 0.60 – 0.69 IV 0.30 – 0.39 VIII 0.70 – 0.79 V 0.40 – 0.49 IX 0.80 – 0.89

Reproductive activity was determined by calculating the proportion of

sexually mature Oligochaeta that is those with a fully formed reproductive system, not in the whole population, but only among individuals, which were capable of reproducing thanks to their size.

RESULTS

The average density of both species for the whole year was similar: L. hoffmeisteri – 910, T. tubifex – 1045 individuals m-2, while their size structure was different (fig. 1). In the first case, almost 70% of the population consisted of individuals of average size, belonging to classes IV to VI (width of the body from 0.30 to 0.59 mm), whereas in the population of T. tubifex small individuals were decidedly the most numerous, belonging to size class III (body width from 0.20 to 0.29 mm), constituting as much as 65% of the total number of this species.

Fig. 1. Size structure of the studied oligochaete populations – mean values.


www.oandhs.org

113

In the T. tubifex population, individuals from size class IV proceeded to reproduce, while in the case of L. hoffmeisteri they were slightly larger – class V (tab. 1). Moreover, in analogous classes the proportion of reproducing Oligochaeta was higher in T. tubifex. It is also worth noting that among the largest Oligochaeta no individuals that were not reproducing were found.

The seasonal variability in the reproductive activity of both species displayed similar tendencies, although their

reproductive strategies were different. L. hoffmeisteri individuals capable of reproducing were found on all of the study dates (fig. 2). The lowest proportion, yet still over 20%, was found in the period from 20 July to 15 October, while in the T. tubifex population on 25 May (when there was the maximum proportion of sexually mature L. hoffmeisteri – 90%) and in the period from 5 July (when there were 80% of mature L. hoffmeisteri) to 15 October no sexually mature individuals were found. On the other hand, when sexually mature T. tubifex individuals occurred in the environment, their proportion (from 50 to 100%) was always higher than that for L. hoffmeisteri on analogous dates.

Fig. 2. Share of reproducing individuals in the number of individuals potentially able to reproduce.

Table 1 Percentage share of reproducing individuals in a given size class

Size class L. hoffmeisteri T. tubifex II - - III - - IV - 2 V 8 53 VI 61 78 VII 97 100 VIII 100 100 IX 100 100

J. Żbikowski


114

It should also be pointed out that from 16 January to 16 May 2001, despite the considerable number of individuals reproducing (fig. 3), hardly any small Oligochaeta were found from classes II and III. This rule was true for both species being studied (fig. 4). Fig. 3. Seasonal changes in the numbers of reproducing individuals. Fig. 4. Seasonal changes in the numbers of juvenile individuals – size classes II and III.


www.oandhs.org

115

DISCUSSION

One of the significant elements that allow a particular species to attain ecological success is the ability to adapt the life cycle, including effective reproduction, to the local conditions present in a given environment.

In the studied populations of the two species of Oligochaeta, the reproductive strategies were different. In the case of Limnodrilus hoffmeisteri, individuals capable of reproducing were found throughout the research period. Kennedy (1966) writes that reproduction in this species usually takes place throughout the year and only in exceptional circumstances it is restricted to certain months, although peaks of reproductive activity can occur at different times, depending on local conditions. Żbikowski (1995) obtained similar results when researching the age structure and reproductive activity of Oligochaeta in the Włocławek Dam Reservoir (WDR), which is populated by these animals in large numbers. It can therefore be said, it would seem that the characteristic feature of Limnodrilus hoffmeisteri is continuity of reproduction taking place with varying intensity throughout the year.

A different situation was noted in the case of Tubifex tubifex, because on 25 May and between 5 July and 15 October no sexually mature individuals were found. Similarly, Żbikowski (1995) observed that in the WDR there were no individuals with a developed reproductive system at certain times of the year, despite the fact that some individuals were sufficiently large to be capable of reproduction. The above observations do not appear to be of a universal nature, however, since Bonacina et al. (1996) observed all the life stages of Tubifex tubifex, i.e. cocoons with eggs and embryos as well as immature and mature individuals throughout a whole year of research in the cold profundal (temp. from 5.2 do 6.1°C) of a pumped storage reservoir in North Italy. Similarly in the case of this species being bred in the laboratory, reproduction is continuous (Pasteris et al. 1996). We should note, however, that in these last two cases habitat conditions were rather favourable and stable – cold but oxygenated profundal and laboratory breeding (temp. 20°C, oxygenated water). On the other hand, in the situation when oxygen and thermal conditions displayed considerable seasonal changes (the studied anthropogenic water body and the WDR), the reproductive period of Tubifex tubifex took place only at certain times of the year.

Pasteris et al. (1996) write that one of the characteristic features of the reproduction of Tubifex tubifex is high fecundity and high mortality in the early life stages. This is one of the reasons why this species is very often used in a variety of biological tests, since when the optimal conditions are provided in the laboratory, mortality decreases significantly, which consequently means that considerable quantities of individuals of this species can be obtained within a

J. Żbikowski


116

relatively short time. In contrast, mortality in the early stages is much lower in Limnodrilus hoffmeisteri than in Tubifex tubifex (Bonacina et al. 1996, after Colombo 1982). The results obtained in the present paper fully confirm the above observations. In June, at the time of a relatively high number of reproducing individuals in both species, 233 (ind. m-2) Tubifex tubifex individuals “produced” as many as 4087 (ind. m-2) young individuals (classes: II and III), while in the case of Limnodrilus hoffmeisteri 589 (ind. m-2) mature individuals were the “perpetrators” of merely 534 (ind. m-2) individuals categorised as class II and III.

Unexpectedly, in the period from 16 January to 16 May, when the density of reproductive individuals of both species was also high, no young individuals were found to be present. It is difficult to point unequivocally to a cause of this phenomenon, since on the one hand low temperatures hinder (but do not completely suspend!) the formation of cocoons, growth and development (Kennedy 1966, Reynoldson 1987, Bonacina et al. 1996), while according to other authors (Poddubnaya 1961, Bonomi & Di Cola 1980, Adreani et al. 1984), both taxa are capable of developing even at temperatures of the order of 2-5°C. Another factor that could be responsible for hindering the growth of Oligochaeta are oxygen deficits, although at the end of winter and the beginning of spring, after the ice cover has gone, the oxygenation of the water is usually at its highest, and, besides, a year earlier during the period being studied, the oxygenation of the bottom water was very good (Żbikowski, unpublished data). Bonacina et al. (1996) write that considerable abundance of bottom fauna can place significant constraints on the development of Tubifex tubifex, but in the water body being studied the density of macrobenthos was not high (several thousand individuals m-2) (Żbikowski, unpublished data). The studied water body is, it is true, well stocked with fish, but in winter and early spring the pressure of fish on bottom fauna is not very great due to the low water temperature, and furthermore, the individuals most at risk would be the larger ones, representing an easier to catch and more attractive meal, as far as calories are concerned.

Therefore, in summary we can state that Limnodrilus hoffmeisteri reproduces throughout the year in the water body being studied, whereas Tubifex tubifex only breeds in certain periods, but has a greater reproductive potential. Meanwhile, the survival rate of young L. hoffmeisteri individuals is greater than in the case of Tubifex tubifex.


www.oandhs.org

117

REFERENCES

Adreani L., Bonacina C., Bonomi G., Monti C., 1984, Cohort cultures of Psammoryctides barbatus (Grube) and Spirosperma ferox Eisen: a tool for a better understanding of demographic strategies in Tubificidae, Hydrobiologia 115: 113-19

Bailey R.C., Day K.E., Norris R.H., Reynoldson T.B., 1995, Macroinvertebrate community structure and sediment bioassay results from nearshore areas of North American Great Lakes, J. Great Lakes Res. 21: 42-52

Bonacina C., Pasteris A., Di Cola G., Bonomi G., 1996, Production and population dynamics of Tubifex tubifex in the profundal zone of a freshwater reservoir in N. Italy, Hydrobiologia 334: 141-6

Bonomi G., Di Cola G., 1980, Population dynamics of Tubifex tubifex by means of a new model. In: R.O. Brinkhurst & D.G. Cook (eds), Aquatic Oligochaeta Biology. Plenum Press, New York: 185-203

Dżenderezjan K.G., Unanjan A.S., 1987, Zviaz miezdu massoj ciela i niekotorymi liniejshimi parametrami tubificid na primiere Potamothrix hammoniensis (Michaelsen), In: Freshwater Oligochaeta, materiały 6 konferencji, Ryga : 64-66 (in Russian)

Finogenova N.P., 1996, Oligochaete communities as the mouth of the Neva and their relationship to anthropogenic impact, Hydrobiologia 334: 185-91

Kennedy C., R., 1966, The life history of Limnodrilus hoffmeisteri Clap. (Oligochaeta: Tubificidae) and its adaptive significance, Oikos 17: 158-68

Lang C., Reymond O., 1995, Recovery from eutrophication delayed in the profundal of Lake Neuchatel : Evidence from the oligochaete communities, Revue Suisse de Zoologie 102(4): 907-12

Marcinkowski K., 1999, Hydrochemia pożwirowego zbiornika „Rybnik”. MSc Thesis , N. Copernicus University, Toruń, (in Polish)

Pasteris A., Bonomi G., Bonacina C., 1996, Age, stage and size structure as population state variables for Tubifex tubifex (Oligochaeta, Tubificidae), Hydrobiologia 334: 125-32

Pasteris A., Vecchi M., Bonomi G., 1999, A comparison among different population models for Limnodrilus hoffmeisteri Claparede (Oligochaeta, Tubificidae), Hydrobiologia 406 : 183-89

Poddubnaya T., L., 1961, Feeding of abundant tubificid species in the Rybinsk Reservoir, Tr. Inst. Biologii vodokhranilishch 4(7): 219-31 (in Russian)

Przybylak W., 1998, Zooplankton jeziora Rybnik , MSc Thesis, N. Copernicus University, Toruń, (in Polish)

ReynoldsonT., B., 1987, The role of environmental factors in the ecology of tubificid oligochaetes – an experimental study, Holarctic Ecology 10: 241-48

Reynoldson T.B., Day K.E., Bailey R.C., Norris R.H., 1995, Methods for establishing biologically based sediment guidelines for freshwater quality management using benthic assessment of sediment, Aust. J. Ecol. 20: 198-219

Risnoveanu G., Vadineanu A., 2001, Structural changes within the Oligochaeta communities of the Danube delta in relation with eutrophication, Proc. Rom. Acad., Series B, 1: 35-42

Tatrai I., 1982, Oxygen consumption and ammonia excretion of herbivorous chironomid larvae in Lake Balaton, Hydrobiologia 96: 129-35

Verdonschot P.F.M., 1996, Oligochaetes and eutrophication: an experiment over four years in outdoor mesocosms, Hydrobiologia 334: 169-83

Wiśniewski R., 1978, Effect of predators on Tubificidae groupings and their production in lakes, Ekol.pol. 26(4): 493-512

Żbikowski J., 1995, Struktura populacji pelofilnego makrozoobentosu Zbiornika Włocławskiego, PhD thesis, N. Copernicus University, Toruń (in Polish)




(119-126) 2007



Biological monitoring of the surface Pomeranian rivers (North Poland) on the basis of the macroinvertebrates

Paweł Zdoliński1, Magdalena Lampart-Kałużniacka

Technical University of Koszalin, Department of Environmental Biology

ul. Śniadeckich 2, 75-453 Koszalin, Poland Key words: river, macroinvertebrate, biomonitoring, biotic indices, ecological status

Abstract

The research of benthic invertebrates was conducted in the year 2005 at selected sites of the Parsęta River and its following tributaries: the Radew, the Wogra, the Pokrzywnica and the Gęsia Rivers. The aim of this work was the assessment of water ecological condition on the basis of biotic indices: Saprobe index S, TBI (Trent Biotic Index), the Biological Monitoring Working Party, which has been adapted to the Polish conditions (BMWP-PL), EPT index, and biodiversity index (D). The most advantageous values of the biotic indices were observed at the following sites: Parsęta-Bardy and Pokrzywnica-Sławoborze. The worst water quality was observed in the Gęsia River in Gąski. It has been noticed that even though the indices based on macroinvertebrates still need further testing, they are sensitive to environmental changes and can be used as a tool in the assessment of flowing water quality. 1 Corresponding author: [email protected]


July 05, 2007 November 07, 2007

P. Zdoliński, M. Lampart-Kałużnicka


120

INTRODUCTION

The basic legal document concerning water management in the European Union is Directive 2000/60/EC issued by the European Parliament and the Board on 23 October 2000, which defines a framework for the Community’s activities in the area of water management, known as the Water Framework Directive (WFD). This Directive is a result of more than five-year discussions and negotiations among a wide range of experts from many fields (Mancini 2006). WFD sets a framework for protection and improvement of European surface and ground water quality (including transgenic and underground waters); its final objective is to achieve “a good water status” until the year 2015 (Borja et al. 2007). Water quality monitoring programmes applied so far in Poland were based primarily on physical and chemical parameters. Both in Europe and North America, quality assessment of lotic waters includes biological parameters in the so-called biomonitoring. Such activities consisting in the inclusion of biological indices in water quality assessment are also required in Poland (Kownacki et al. 2002). An analysis and tests of selected biotic indices based on a research into the benthic macroinvertebrates in the Pomeranian rivers are the chief purpose of this paper.

STUDY AREA

The studied rivers as understood by Water Framework Directive (WFD) are situated in an ecoregion of 14 Flatlands of Central Europe. In the typology according to system A provided by WFD Annex II, all rivers under this study are lowland rivers located 200 meters above sea-level; the Parsęta and the Radew are considered as large rivers (catchment area – large 1000-10000 km2) as their catchment areas are 3081.5 km2 and 1092.0 km2, respectively. Characteristics of the investigated Pomerania rivers have been shown in Table 1.


The samples were taken in May 2005 from selected sites on the Pomeranian rivers (Table 1). At each site, four quantity samples and one quality sample were taken. A hand net was used (in compliance with PN-EN 27828:2001 standard). The size of the openings in the net was 0.5 mm, while the intake surface was 400 cm2. The samples obtained were conserved with 4% formaldehyde solution and transported to the laboratory. Before identification of the organisms, the samples were rinsed on a benthic screen with 0.5 mm mesh diameter, by pouring through it successive portions of the sediment diluted with

Biological monitoring of the surface Pomeranian rivers

www.oandhs.org

121

water. The samples were placed under a Nikon Eclipse E 400 stereoscope microscope. For the assessment of taxonomic composition, appropriate keys and conductors were used. Straight majority of the collected material was identified to species level. In cases where such precise identification was impossible, organisms were identified to family level. For the purpose of the assessment, density and number of identified taxa were used. Additionally, on the basis of the studies by Woodiwiss (1964), Błachuta et al. (2002), Kownacki et al. (2004), Kownacki and Soszka (2004), as well as Pantle and Buck (1955), the following biotic indices were calculated: TBI (Trent Biotic Index), BMWP-PL (the Biological Monitoring Working Party), adapted to the Polish conditions, S saprobe index, EPT index: ratio of the number of Ephemeroptera, Plecoptera and Trichoptera to the number of all taxa in a sample, as well as a biodiversity index (D). In calculating the above indices, the methodically required level of taxonomic identification was used.

RESULTS

The largest concentration of organisms was recorded at the sites no. 4 (1156 ind. m-2) and no. 1 (850 ind. m-2) (Tab. 2). The smallest concentration values were found tributaries at the site no. 2 (150 ind. m-2). The largest diversity was found at the sites no. 1 (22 ind.) and 6 (21 ind.). The smallest diversity – 13 ind. - was found at the site no. 2.

The TBI index (cf. Tab. 3) reached the highest value (a range of 6-8) at the sites no. 1 and 3. The lowest value – the satisfactory level – was found at the site no. 4. The remaining rivers covered by the study were characterized, in

Table 1 Characteristics of the investigated Pomerania rivers

River Site no. Locality

Distance from the spring

(km)

Width (m)

Depth (m)

The river-bed

The surrounding area Pollution

Parsęta 1 Bardy 102.0 12.0 2.5 sand-mud

meadows and grazing land missing data

2 Stare Dębno 35.0 12.0 3.0 mud mixed forest missing data Radew 3 Białogórzyno 64.5 12.0 2.5 sand single leafy trees missing data 4 Żydowo 19.5 6.0 1.0 stone leafy forest missing data

Gęsia 5 Gąski 7.0 3.0 0.5 sand single leafy trees spot sewage discharge

Pokrzyw-nica 6 Sławoborze 12.5 3.0 0.4 sand-

stone

single trees, industrial

infrastructure missing data

Wogra 7 Połczyn Zdrój 16.0 4.0 1.2 sand-

mud meadows and grazing land

spot sewage discharge



122

accordance to TBI, by a moderated water quality level. The index of BMWP-PL had the highest values at the sites no. 1 and 6. It reached a satisfactory level at the sites no. 5 and 2 having the values of 30 and 37, respectively. It reached a moderate level at the remaining sites. The saprobe index reached a good level at all sites investigated. It reached the most favourable values at the sites no. 2 (1.55) and no. 6 (1.59). At the sites no. 4 and 5 the values of the index were the highest, thus the least favourable. The most favourable values of the EPT index were noted at the sites no. 6 and 1, while the lowest EPT value was observed at the site no 4. The largest biodiversity index was found at the sites no. 1 and 6; the lowest value was recorded at the site no 5. Comparing the obtained values of biotic indices at the two referential sites (sites no. 1 and 2) with the results of Błachuta et al. (2002) a slight deterioration in the indices can be noticed. The

Table 2 Density and diversity at investigated sites

Site no. Density [ind. m-2] Diversity [ind.]

1 850 22 2 150 13 3 269 16 4 1156 18 5 494 15 6 750 21 7 656 18

Table 3 List of indices at investigated sites

Index Site no. TBI BMWP-PL S EPT D

1 7 good

58 moderate

1.73 good 0.50 7.51

2 6 moderate

37 satisfactory

1.55 good 0.49 5.97

3 7 good

46 moderate

1.78 good 0.27 6.58

4 4 satisfactory

41 moderate

1.97 good 0.12 5.88

5 5 moderate

30 satisfactory

1.93 good 0.43 5.56

6 6 moderate

51 moderate

1.59 good 0.54 7.30

7 6 moderate

41 moderate

1.76 good 0.44 6.39


www.oandhs.org

123

smallest differences have been observed in EPT index and the biggest in BMWP-PL.

DISCUSSION

Biological methods record long-term changes in a given aquatic ecosystem, which is an undeniable advantage (Fleituch et al. 2002). These changes are difficult to demonstrate while analysing physicochemical parameters as they characterize water quality only at the time of sample collection.

These studies based on macroinvertebrates have shown that the sites in Bardy (on the Parsęta) and Sławoborze (on the Pokrzywnica) have the most advantageous ecological conditions. It has been proved by high values of the following indices: TBI, BMWP-PL, EPT and D (Tab. 3). Recently conducted water and sewage-system works in these areas have decreased the amount of sewage getting into surface waters. Another important factors which led to water quality improvement in the lower Parsęta River were water self-cleaning processes which consist in transforming organic matter into non-organic one (Żmudziński et al. 2002). The result of biological and biochemical water self-cleaning processes is a change in aquatic flora and fauna from organisms typical of polluted waters into the ones characteristic of clean waters which are devoid of big amounts of organic substances (Gomółka & Szaynok 1997).

It is also worth noticing that river-beds of the Parsęta River in Bardy and the Pokrzywnica River in Sławoborze were dominated by sand (Tab. 1). The quality of river-bed is an important structure formation factor in benthic biocenoses (Lampert & Sommer 1996). In many rivers characterized by sand bottom the surface of the river-bed is variable at different places and at different times; behind moving shoals there are sediments which temporarily create environment for fauna typical of stable waters (Tarwid et al. 1988). Such environment, by creating good living conditions such as accessibility to food and favourable water flow could have contributed to greater biodiversity in sand-bottom rivers than in rivers with dominant stone bottom and rapid water flow (Tab. 2). These assumptions have been proved by Mikulski (1974) who claims that the structure of the river-bed influences the number of benthic oligochaetes and the species variety in a given biotope.

According to the obtained data, the worst ecological conditions were in Gąski (on the Gęsia River) and in Żydowo (the Radew River). This was indicated by: unfavourable values of TBI, BMWP-PL, and indices S and D (Tab. 3). In the case of site no. 5 this situation could have been caused by spot sewage discharge into the river. Sewage channelling can have considerable and variable influence on the number of benthic organisms because it raises water temperature, what according to Tarwid (1988) and Allan (1998) makes it



124

difficult for organisms to breathe. Such situation can contribute to the changes in the amount ratios between species, which can lead to the changes in the average benthos abundance (Kajak et al. 1988) and lower values of calculated indices. Poor water quality at site no. 4 can be attributed to the existence of a pumped-storagepower plant on Kwiecko and Kamienne Lakes from which the Radew River flows. Constant fluctuation of the river level may cause stress behaviours among macroinvertebrates, which result in their lower amount and poorer diversity.

According to the Report (2004), the Gęsia River has been classified as a flow where high water quality will be difficult to obtain by 2015. Therefore, it is extremely important to take rapid measures aimed at improving water quality of this tributary. This could be achieved by developing water and sewage systems in this region of the Parsęta tributary.

Considerable differences between the values of BMWP-PL index in 2002 and 2005 (Tab. 4) at the sites prove that frequency and time play an important role in collecting samples of benthos. Błachuta et al. (2002) based their research on macroinvertebrates samples collected twice, in June and September. The difference obtained between indices in 2002 and 2005 can be caused by a different method of sample collection.

If we compare all biotic indices used in the study, the best ecological conditions of the rivers have been shown by S and D indices. In the cases of TBI and BMWP-PL the same rivers usually showed worse water quality. However, it must be noticed that TBI and BMWP-PL indices use a family as a unit of taxonomic identification, which according to Czerniawska-Kusza (2005) and Graça & Coimbra (1998) may lead to greater overstating or understating of water quality than in the case of indices based on species identification. Yet, TBI and BMWP-PL indices are more frequently used because they require less sophisticated taxonomic knowledge, are less laborious and therefore more economical (De Pauw et al. 2006).

Table 4 Results obtained at reference sites in the years 2002 (Błachuta et al.) and 2005 (own research)

Parsęta-Bardy Parsęta-Stare Dębno Site Index 2002 2005 2002 2005 TBI 10 7 9 6 BMWP-PL 171 58 135 37 Saprobe index S 1.70 1.73 1.54 1.55 EPT 0.51 0.50 0.50 0.49


www.oandhs.org

125

Within the last decades, increasing effort has been devoted to designing a more effective use of macroinvertebrates as monitoring and assessment tools for management of water resources (Buffagni et al. 2000, Lorenz et al. 2004, Czerniawska-Kusza 2006).

Summing up, the conducted studies have shown that using macroinvertebrates in water quality assessment provides positive and promising results because they show noticeable sensitivity to environmental changes. However, methods based on these studies which are used in water quality assessment require further verification and testing on different river types.

REFERENCES

Allan J. D., 1998, Ekologia wód płynących, [Ecology of flowing waters], Warszawa, Wydawnictwo Naukowe PWN, pp. 450 (in Polish)

Błachuta J., Żurawska J., Brzostek-Nowakowska J., Martynko-Pluta E., Miluch J., Kassyk W., Wierzchowska E., Berendt I., Zakościelna A., 2002, Monitoring wód powierzchniowych województwa zachodniopomorskiego. Makrozoobentos, [Monitoring of surface waters in Zachodniopomorskie Province. Macrozoobenthos], Maszynopis, pp. 62 (in Polish)

Borja A., Josefson A. B., Miles A., Muxica I., Olsgard F., Philips G., Rodríguez J. G., Rygg B., 2007, An approach to the intercalibration of benthic ecological status assessment in the North Atlantic ecoregion, according to the European Water Framework Directive, Marine Pollution Bulletin, 55: 42-52

Buffagni A., Crosa G., Harper D. M, Kemp J. L., 2000, Using macroinvertebrate species assemblages to identify river channel habitat units: an application of the functional habitat concept to a large, unpolluted Italian river (River Ticino, Northern Italy), Hydrobiologia, 435: 213-225

Czerniawska-Kusza I., 2005, Comparing modified biological monitoring working party score system and several biological indices based on macroinvertebrates for water-quality assessment, Limnologica, 35: 169-176

De Pauw N., Gabriels W., Goethals P. L. M., 2006, River Monitoring and Assessment Methods Based on Macroinvertebrates, [in:] Biological Monitoring of Rivers. Applications and Perspectives, Eds. Ziglio G., Siligardi M., Flaim G., John, The Atrium, Southern Gate, Chichester, West Sussex, Wiley & Sons, Ltd, 113-170

Fleituch T., H. Soszka, D. Kudelska, A. Kownacki, 2002, The use of macroinvertebrates as indicators of water quality in rivers: a scientific basis for Polish standard method, Large Rivers vol. 13, Arch. Hydrobiol. Suppl. 141/3 no 3-4: 225-239

Gomółka E., Szaynok A., 1997, Chemia wody i powietrza, [Chemistry of water and free air], Wrocław, Oficyna Wydawnicza Politechniki Wrocławskiej, pp. 433 (in Polish)

Graça M. A. S., Coimbra C. N., 1998, The elaboration of indices to assess biological water quality. A case study, Wat. Res., Vol. 32, No. 2: 380-392

Kownacki A., Soszka H., Fleituch T., Kudelska D. (eds.), 2002, River biomonitoring and benthic invertebrate communities, Warszawa – Kraków, Institute of Environmental Protection, Karol Starmach Institute of Freshwater Biology, Polish Academy of Sciences, pp. 88

Kownacki A., Soszka H., Kudelska D., Flejtuch T., 2004, Bioassessment of Polish rivers based on macroinvertebrates. In: Geller W. et al. (eds.). 11th Magdeburg seminar on Waters In Central and Eastern Europe: Assessment, Protection, Management. Proceedings of the international conference, 18-22 October 2004 at the UFZ. UFZ-Bericht, 18/2004: 250-251



126

Kownacki A., Soszka H., 2004, Wytyczne do oceny stanu rzek na podstawie makrobezkręgowców oraz pobierania prób makrobezkręgowców w jeziorach, [Guidelines for the evaluation of the status of rivers on the basis of macroinvertebrates and for intakes of macro-invertebrate samples in lakes], Warszawa, pp. 51 (in Polish)

Lampert W., Sommer U., 1996, Ekologia wód lądowych, [Ecology of fresh waters], Warszawa, Wydawnictwo Naukowe PWN, pp. 390 (in Polish)

Lorenz A., Hering D., Feld C. K., Rolauffs P., 2004, A new method for assessing the impact of hydromorphological degradation on the macroinvertebrate fauna of five German stream types, Hydrobiologia, 516: 107-127

Mancini L., 2006, Organization of Biological Monitoring in the European Union, [in:] Biological Monitoring of Rivers. Applications and Perspectives, Eds. Ziglio G., Siligardi M., Flaim G., Jonhn, The Atrium, Southern Gate, Cichester, West Sussex, Wiley & Sons, Ltd, 171-201

Mikulski J. S., 1974, Biologia wód śródlądowych, [Biology of inland waters], Warszawa, Państwowe Wydawnictwo Naukowe, pp. 434 (in Polish)

Pantle E., Buck H., 1955, Die biologische Überwachung der Gewasser und die Darstellung der Ergebnisse, Gas und Wasserfach, 96: 604 (in German)

prPN-EN 27828, 2001, Jakość wody – Metody pobierania próbek do badań biologicznych – Wytyczne do pobierania makrobentosu z użyciem siatki ręcznej, [Methods to take samples for biological examinations: guidelines for macrobenthos intake with the use of a hand net], Polski Komitet Normalizacyjny, pp. 10 (in Polish)

Raport - Charakterystyki obszaru dorzecza i ich analizy wg artykułu 5 Ramowej Dyrektywy Wodnej na przykładzie obszaru pilotażowego – dorzecza Parsęty, [Report - Characteristics and analyses of catchment areas following article 5 of the Water Framework Directive based on pilot Parsęta catchment area], 2004, Maszynopis (in Polish)

Tarwid K. (ed), Kajak Z., Spodniewska I., Wróbel S., 1988, Ekologia wód śródlądowych, [Ecology of inland waters], Warszawa, Państwowe Wydawnictwo Naukowe, pp. 322 (in Polish)

Woodiwiss F. S., 1964, The biological system of stream classification used by the Trent River Board, Chemistry and Industry, 11: 443-447

Żmudziński L., Kornijów R., Bolałek J., Górniak A., Olańczuk-Neymann K., Pęczalska A., Korzeniewski K., 2002, Słownik hydrobiologiczny (ochrona wód, terminy, pojęcia i interpretacje), [Hydrobiology dictionary (water protection, terms, concepts and interpretations)], Warszawa, Wydawnictwo Naukowe PWN, pp. 285 (in Polish)

Documents

Oceanological and Hydrobiological Studies - PTHpth.home.pl/pobierz/Oceanological_and_Hydrobiological... · 2008-08-03 · Vol. XXXVI Supplement 4 2007 Oceanological and Hydrobiological