Embed Size (px)
Citation preview
Cm
Ga
b
a
ARRA
KANBPPP
1
ciaPoemoZKi
m(
0h
Ecological Engineering 58 (2013) 214– 227
Contents lists available at SciVerse ScienceDirect
Ecological Engineering
j ourna l ho me pa g e: www.elsev ier .com/ locate /eco leng
apabilities of alders (Alnus incana and A. glutinosa) to grow inetal-contaminated soil
abriela Lorenc-Plucinskaa,∗, Marta Walentynowicza, Alicja Niewiadomskab
Institute of Dendrology, Polish Academy of Sciences, Parkowa 5, 62-035 Kórnik, PolandDepartment of Agricultural Microbiology, Poznan University of Life Sciences, Szydłowska 50, 60-656 Poznan, Poland
r t i c l e i n f o
rticle history:eceived 24 January 2013eceived in revised form 23 May 2013ccepted 1 July 2013
eywords:lnus2 fixationacterial populationshosphomonoesteraseshenolic compoundshytostabilization
a b s t r a c t
This study examined the effects of metal-polluted soil on growth, biomass and uptake of trace metalsand nutrients in Alnus incana and A. glutinosa seedlings. The rate of nitrogen fixation, counts of micro-bial groups, activities of phosphomonoesterases, and phenolic compounds in soil were also determined.Seedlings of various origin were grown for 158 days in forest soil (control) and in soil from a copper smelterarea, with low nutrient content and high concentrations of Cu (1510 mg kg−1) and Pb (490 mg kg−1). Bothalder species accumulated in their roots Cu and stored Pb, Zn (A. incana ≈ A. glutinosa) and Cd (A. gluti-nosa > A. incana). Concentrations of Cu, Pb, Zn and Cd were lower in shoots than in roots. Concentrationsof Cu, Zn, Cd and Pb in leaves of both alder species were within normal ranges. Nutrient weight pro-portions P:K:Ca:Mg (N = 100) for leaves of Alnus spp. growing in polluted soil were higher than in thecontrol. Alder growth in polluted soil was characterized by slight changes in total biomass of seedlingsand nodules. Nodules stored Cu, Cd (A. incana > A. glutinosa), Pb and Zn, while concentrations of P andCa were lower in nodules than in the control. N levels in leaves of alders grown in polluted soil were
generally lower than those of alders grown in control soils. We also recorded a reduction in the rate of N2fixation in nodules when alders were grown in polluted soil. In the rhizosphere in polluted soil, actinobac-teria (actinomycetes) and copiotrophs were less numerous, while oligotrophs were more numerous. Alsoactivities of phosphomonoesterases were strongly reduced, while concentrations of water-soluble phe-nols increased. The results suggest that both species of Alnus grow well in heavily polluted soil, in spiteof accumulation of toxic metals in their roots and nodules and a decreased rate of N2 fixation.
im
gsdocsiN
. Introduction
Trace elements are widespread in individual layers of the Earth’srust, also in soil. Higher concentrations of Cu, Ni, Mn, Zn, Cd and Pbn the surface layer of the soil are usually caused by human activitynd lead to soil contamination or soil pollution. Kabata-Pendias andendias (2001) suggest that in contaminated soil, concentrationsf trace metals exceed average levels but do not have a negativeffect on the natural environment, whereas in polluted soil, traceetals reach total critical levels, toxic for living organisms, most
ften determined as (in mg kg−1): Cu 60–125, Cr 75–100, Ni 100,
n 70–400, Mn 1500–3000, Cd 3–8 and Pb 100–400 (Alloway, 1995;abata-Pendias and Pendias, 2001). Soil pollution with trace metalss mostly due to steel mills and smelters, other branches of metal
∗ Corresponding author. Tel.: +48 618170 033; fax: +48 618170 166.E-mail addresses: [email protected] (G. Lorenc-Plucinska),
[email protected] (M. Walentynowicz), [email protected]. Niewiadomska).
2svL
tahr
925-8574/$ – see front matter © 2013 Elsevier B.V. All rights reserved.ttp://dx.doi.org/10.1016/j.ecoleng.2013.07.002
© 2013 Elsevier B.V. All rights reserved.
ndustry, chemical industry, pulp and paper mills, tanneries andining.This study assessed the capabilities of alders (Alnus incana and A.
lutinosa) to grow in polluted soil from the buffer zone of a coppermelter, for their potential use for remediation and revegetation ofegraded areas. Polluted soil in the study area is harmful for livingrganisms not only because of high concentrations of trace metals,lose to the upper permissible limits (Cd, Zn) or exceeding permis-ible levels (Cu, Pb), but also as a result of unfavourable changesn pH of the soil solution and concentrations of macronutrients:, P, K, Ca, Mg and especially an excess of S (Stefanowicz et al.,009; Stobrawa and Lorenc-Plucinska, 2007). In poplars (Populuspp.) this has led to abnormal root and shoot development, reducediability and increased sensitivity to biotic stress (Stobrawa andorenc-Plucinska, 2008).
Alders are pioneer woody species of high ecological impor-
ance, commonly used as nurse trees for other plant species. Forlders, nutrient deficits in the soil, especially of N and P, are lessarmful than for other tree species, because the symbiosis of alderoots with actinobacteria (actinomycetes) of the genus Frankia
gical E
efp(i(ismeatcase1tK2
ftaomusmsaadsdmeFp
2
2
nWW(ofteKlrpn(i
gfii
(zElZtdsattCsuSgaesh
rmyreRwwrz
2
scf
2
sbso1OheFapTmw4d1ca
G. Lorenc-Plucinska et al. / Ecolo
nables N2 fixation from the air, while symbiosis with mycorrhizalungi and the associated microbial communities, as well as activehosphatases in root exudates, enable greater access to nutrientsPawlowski, 2011; Roy et al., 2007). In particular, the availabil-ty of P and some cations (Mg2+, Mn2+) in the soil is increasedKuznetsova et al., 2011). In addition, alder leaves are character-zed by low retranslocation of nitrogen from ageing leaves to thetems (Kuznetsova et al., 2010). N-rich alder leaf litter is thereforeineralized much faster than that of other tree species (Claessens
t al., 2010). By extension, the improved nitrogen status of the soilccelerates microbial decomposition of the nitrogen-poor leaf lit-er of other species, creating favourable conditions for microbialommunities (Lefranc ois et al., 2010; Wenzel, 2009). Alders have
high water demand, but unlike in many other trees, their rootystems are well adapted to water deficits (Claessens et al., 2010),nabling them to partially tolerate drought (Whitbread-Abrutat,997). Alders have been used for the reclamation of sites con-aminated with toxic levels of trace elements (Dickinson, 2000;uznetsova et al., 2010, 2011; Lefranc ois et al., 2010; Markham,005; Pourrut et al., 2011; Vandecasteele et al., 2008).
Our working hypothesis was that alders can be recommendedor the revegetation of areas polluted with phytotoxic concentra-ions of trace metals, due to their tolerance to stress conditionsnd their ability to grow in low-nutrient environments. The majorbjective of the present study was to investigate the effect of traceetal pollution of the soil on growth, biomass production and
ptake and transfer of metals and nutrients in one-year-old aldereedlings. Our second objective was to investigate the effect of traceetals on the activity of nitrogen-fixing actinobacteria (Frankia
p.). The study involved also counts of selected microorganismsnd measurements of activity of soil enzymes. Additionally, wessessed the level of phenolic compounds in soil, as a potentialefence response of alder to the harmful trace metals. We usedeedlings from three provenances, to take into account potentialifferences in their genotypes and initial growth conditions, whichight affect plant health as well as form and growth rate (Claessens
t al., 2010) and, potentially, their response to metal-polluted soil.inally, we discuss the suitability of alders for the revegetation andhytostabilization of soils heavily polluted with toxic trace metals.
. Materials and methods
.1. Plant material, growth conditions and treatments
One-year-old seedlings of A. incana (L.) Moench and A. gluti-osa (L.) Gaertn. were obtained from 3 forest nurseries (Krzyzielkopolski 52◦52′ N, 16◦00′ E; Rzepin 52◦21′ N, 14◦50′ E andolsztyn 52◦07′ N, 16◦07′ E) and represent 3 provenances: Krzyz
Kr), Rzepin (Rp) and Wolsztyn (Wl) from western Poland. Somef the seedlings developed there from seeds of A. incana collectedrom 60- to 80-year-old trees, natural forest stands located withinhe above nurseries as well as seeds of A. glutinosa from the nurs-ry in Wolsztyn. Seedlings of A. glutinosa represent provenancesr and Rp came from seed orchards (trees several decades old)
ocated within Krzyz and Rzepin nurseries. Each provenance rep-esented local gene pools. In each species, seedlings of differentrovenances differed in stem height and root weight (Table 1). Sig-ificant differences were found also between species in stem heightA. incana > A. glutinosa, p = 0.019) and root weight (A. glutinosa > A.ncana, p = 0.02).
Single seedlings were planted in 2.7 dm3 pots on 16 March andrown in a plastic tunnel for 158 days, to 31 August. The pots werelled either with unpolluted soil (control) collected from exper-
mental forest of the Institute of Dendrology in Kórnik, Poland
Swcs
ngineering 58 (2013) 214– 227 215
52◦14′ N, 17◦05′ E) or with polluted soil collected from the bufferone of the “Głogów” Copper Smelter in Zukowice (51◦40′ N, 15◦58′
), within a distance of 1.6 km from the smelter. Poplars (Popu-us spp.) aged about 35 years are found at both sites (Kórnik and˙ ukowice). In Zukowice, the poplars are characterized by satisfac-ory growth in height but significantly lower trunk diameter, poorlyeveloped tree crown and they rarely shed old/dead branches. Soilamples were collected by digging into the soil about 5–20 cm deep,fter removal of leaf litter and other organic remains in six dis-inct locations of the unpolluted (control) and polluted sites. Bothhe study sites were postagricultural lands with soils classified asambisols (FAO): loamy at the polluted site (according to USDApecification: 74% sand, 25% silt and 1% clay) and sandy at thenpolluted (control) site (88% sand, 11% silt and 1% clay) (Table 2).oil sampling was performed in early spring (March), before therowing season, to minimize the effect of local plants on microbialctivity in the soil. A total of 200 alder seedlings were cultivated, asach experimental variant was represented by 15–17 plants of eachpecies. Seedlings were watered manually to maintain relative soilumidity of 60–80%.
After 158 days of the pot experiment, leaves, stems, roots andoot nodules of 12 randomly selected seedlings were collected fororphological, elemental and actinorhizal nitrogen fixation anal-
ses. Simultaneously, the fraction of soil adhering to roots (closehizosphere) were taken from each pot for microbiological andnzymatic analysis and determination of phenolic compounds.oots and nodules used for morphological and elemental analysisere manually separated from the soil and quickly but thoroughlyashed in tap water. Living fine roots were separated from dead
oots based on their lighter colour and greater resilience. Mycorrhi-ae associated with roots were regarded as part of the roots.
.2. Plant growth analysis
The biomass of seedlings at the end of the experiment was mea-ured as dry weight (DW, after drying at 70 ◦C for 48 h or until aonstant dry weight was obtained). It was determined separatelyor leaves, stems, roots and nodules of each seedling.
.3. Elemental analysis of the soil and plants
The chemical composition of the soil from polluted and controlites was analyzed before the experiment. The soil samples wereriefly air-dried, crushed and passed through 2 mm plastic meshieves. Particle size distribution was determined by a combinationf sieving and sedimentation. Soil pH was measured in H2O or in
n KCl at a ratio of 1:5 (w/v) with a pH-meter (HACH HQ40d).rganic matter was determined according to Tiurin’s method afterot digestion of soil samples with K2Cr2O7 and H2SO4 in the pres-nce of Ag2SO4 as catalyst and titration of the excess K2Cr2O7 witheSO4/(NH4)2SO4·6H2O (Mocek and Drzymała, 2010). For furthernalyses, air-dried and sieved soil samples were ground to fineowder using an agate ball mill (Analysette 3 Spartan, FRITSCH).otal N (organic and N-NH4) was determined with the Kjeldahlethod. A subsample of soil (0.5 g) was dissolved in 12 ml of H2SO4ith 2 tablets of Kjeltabs (K2SO4 + CuSO4·5H2O) and digested at
40 ◦C for 1 h (FOSS TecatorTM Digestion Unit Auto) followed byistillation on KjeltecTM 2300 Analyzer Unit (FOSS Tecator), using% boric acid in titration. Total S was analyzed by means of aarbon–sulfur analyser (LECO SC. 144 DRPC), after O2-combustiont 1400 ◦C. Bioavailable forms of N (N-NH4 and N-NO3) and S (S-
O4) were extracted from air-dried soil samples with de-ionizedater (17 M�) at a ratio of 1:5 (w/v) for 1 h and filtered throughellulose acetate membrane syringe filter (0.45 �m), and mea-ured using ion chromatography (Dionex, DX 100 with Ionpac
216 G. Lorenc-Plucinska et al. / Ecological Engineering 58 (2013) 214– 227
Table 1Height and biomass of one-year-old seedlings (stems and roots) and root nodules of Alnus incana and A. glutinosa from 3 provenances (Kr, Wl and Rp) before the potexperiment (early March).
Alnus species Seedling origin Height (cm) Biomass (g DW)
Stems Stems Roots Seedlings Root nodules
A. incana Kr 43.5 ± 4.1 2.4 ± 0.6 1.5 ± 0.4 4.0 ± 1.0 0.07 ± 0.02Rp 38.8 ± 1.1 2.9 ± 0.3 2.6 ± 0.4 5.6 ± 0.6 0.08 ± 0.01Wl 58.3 ± 1.6 3.1 ± 0.5 1.2 ± 0.4 4.5 ± 0.9 0.10 ± 0.03p 0.033 ns 0.027 ns ns
A. glutinosa Kr 34.2 ± 1.6 2.4 ± 0.3 2.8 ± 0.3 5.2 ± 0.5 0.04 ± 0.01Rp 48.2 ± 2.5 3.4 ± 0.3 2.9 ± 0.2 6.4 ± 0.4 0.08 ± 0.01Wl 49 ± 3.1 2.7 ± 0.6 1.3 ± 0.4 4.0 ± 1.0 0.06 ± 0.02
ns
M nt.
CuSdamue(biAshc(ia(ab
ae5(pfed
psnGfatmK
TP
MS
p 0.046
ean values ± SE of 6 random seedlings; p – level of significance; ns – not significa
S12A for N-NH4 and Dionex ICS 1100 and Ionpac AS9-HC col-mn for N-NO3 and S-SO4). Dionex Six Cation Standard-II andeven Anion Standard II were used for calibration. For total Petermination, the soil was mineralized with HClO4 and digestedt 290 ◦C (FOSS TecatorTM Digestion Unit Auto). The digest wasade up to 20 ml and analyzed by molybdenum–vanadate method
sing a Hach-Lange DR 3800 spectrophotometer. Available P wasxtracted with 0.5 M sodium bicarbonate at pH 8.5 (ratio 1:5, w/v)Olsen’s method). After filtration through cellulose acetate mem-rane syringe filter (0.45 �m), the anions were determined by
onic chromatography (Dionex ICS 1100, equipped with the IonpacS9-HC column). To determine the total soil metal concentrations,amples of 0.5 g were digested with 10 ml of HClO4 for 24 h andeated till dry at 290 ◦C (FOSS TecatorTM Digestion Unit Auto). Thelear solution was then made up to 20 ml with de-ionized water17 M�). Concentrations of major metals (K, Mg, Ca, Fe and Zn)n the extracts were subsequently analyzed on a flame furnacetomic absorption spectrometer (Varian AA 280 FS). Trace metals
Pb, Cu, Cd, Cr and Mn) were analyzed by graphite furnace atomicbsorption spectrometer (Varian AA280 equipped with Zeemanackground correction and GTA 120). Bioavailable metals werers
able 2hysicochemical characteristics of unpolluted (control) and polluted soil before the pot e
Characteristic Total forms
Control soil Pollute
Texture (% sand:silt:clay) 88:11:1 74:25:pH (H2O) 7.01 ± 0.01 5.92 ±pH (1 n KCl) 6.89 ± 0.04 5.28 ±Organic matter (%) 3.51 1.44N (%) 0.178 ± 0.001 0.125 ±N-NH4 (mg kg−1)
N-NO3 (mg kg−1)
C (%) 2.03 ± 0.033 0.778 ±C:N 11.40 6.30P (mg kg−1) 505 ± 2 470 ± 3K (mg kg−1) 808 ± 7 2630 ±Mg (mg kg−1) 847 ± 16 1080 ±Ca (mg kg−1) 8927 ± 203 1970 ±S (mg kg−1) 2180 ± 30 3708 ±Fe (mg kg−1) 5760 ± 80 8090 ±Cu (mg kg−1) 4.0 ± 0.1 1510 ±Cr (mg kg−1) 7.9 ± 0.1 20 ± 1*
Mn (mg kg−1) 168.0 ± 0.7 420 ± 2Zn (mg kg−1) 25.0 ± 0.4 72 ± 4Cd (mg kg−1) 1.22 ± 0.07 1.47 ±Pb (mg kg−1) 38.1 ± 0.6 490 ± 2
ean values ± SE of 6 independent replicates.ignificant differences between control and polluted soil:** p < 0.01.
*** p < 0.001.**** p < 0.0001.
0.048 ns ns
ssessed by the method of Quevauviller et al. (1997). Briefly, EDTAxtraction was carried out by shaking 5 g of soil subsample with0 ml of a solution of 0.05 M EDTA as an ammonium salt solutionpH ≈ 7) for 1 h at 20 ◦C. The suspension was filtered through filteraper (porosity 0.4–1.1 �m). The filtrates were analyzed by flameurnace or graphite furnace GTA 120 atomic absorption spectrom-try (Varian AA280 FS and Varian AA280Z), depending on requiredetection limits.
Quality control was ensured by the use of triplicate analyseserformed on all samples, the use of blank samples and certifiedtandards: ISE sample 912 (WEPAL) for N, S and P; CRM Contami-ated Soil-SS-2 (EnviroMATTM) and Chinese Soil 4, (PROMOCHEMmbH, No. GBW07404) for total metals, and BCR®-483 (Institute
or Reference Materials and Measurements, Belgium) for bioavail-ble metals. Values of most samples deviated less than ±10% fromhe certified values. The analyses were performed in the Depart-
ent of Ecology of the Institute of Botany, Polish Academy Sciences,raków, Poland.
Plant organs (leaves, stem, roots and nodules) were dried sepa-ately (70 ◦C, 48 h), ground in a ball mill and sieved to 1 mm particleize. Subsamples (0.2 g) were digested in 8 ml of HCl (37%) and
xperiment.
Bioavailable forms
d soil Control soil Polluted soil
1 0.04****
0.01****
0.005***
0.419 ± 0.003 0.302 ± 0.01****
42 ± 1 2.45 ± 0.03****
0.038****
0 20.3 ± 0.7 174 ± 8***
100*** 54.6 ± 0.5 236 ± 8****
20*** 54 ± 2 71 ± 3**
60**** 4690 ± 40 1010 ± 50****
68*** 403 ± 16 570 ± 20**
70**** 346 ± 7 440 ± 20**
50**** 1.68 ± 0.04 1270 ± 30****
*** 0.186 ± 0.008 10 ± 1***
0**** 108 ± 3 200 ± 10***
**** 5.2 ± 0.1 24 ± 2***
0.03** 0.311 ± 0.004 0.42 ± 0.01***
0**** 9.6 ± 0.1 311 ± 7****
gical E
HdpSECt9tIlbfba7TfK
fi(s
2
aGftaavvECiadC
2
afiDdwoi
2
amTnan
2
a(spcwTt
2
wtyehmm
T
a
S
wt
(
�
(Mftbewpi
3
3
ScgCi
G. Lorenc-Plucinska et al. / Ecolo
NO3 (65%) at a 3:1 ratio for 30 min at 210 ◦C during microwaveigestion (Multiwave 3000, Anton Paar, GmbH, Austria; Step 1:ower 1400 W, ramp time 10 min, hold time 20 min, fan 1 andtep 2: power 0 W, ramp time 0 min, hold time 15 min, fan 3).xtracts were subsequently analyzed for P, K, Ca, Mg, Fe, Cu, Zn,d and Pb concentrations by using inductively coupled plasmaime-of-flight (TOF) mass spectrometer (Spectrometer OptiMass500 ICP-TOF-Ms, GBC). N and S were measured by dry combus-ion using Elemental Combustion System CHNS-O 4010 (Costechnstruments, Italy/USA). Each plant sample was prepared and ana-yzed in triplicate. For every 6 plant samples, we measured also onelank sample and one certified sample: pine needles (SRM 1575a,rom the National Institute of Standards and Technology, USA);eech leaves (BCR®-100, from the Institute for Reference Materialsnd Measurements, Belgium), or bush branches and leaves (NCS Dc3349, from the China National Analysis Centre for Iron and Steel).he recovery rate was 91.5% for N, 94.2% for S, 93.9% for Fe, 91.9%or Cu, 95.9% for Zn, 92.5% for Cd, 98% for Mg, 91.2% for P, 93.8% for
and 101.2% for Ca, as compared to certified values.For each alder species and seedling origin, bioconcentration
actors (BCF) for Cu, Zn, Cd and Pb were calculated by divid-ng metal concentrations (mg kg−1 DW) in above-ground shootsleaves + stems) by total metal concentrations (mg kg−1 DW) in theoil (Rosselli et al., 2003).
.4. Nitrogen fixation
The rate of N2 fixation by Frankia in symbiosis with alders wasssessed as acetylene reduction activity (ARA) (Huss-Danell, 1978;aulke et al., 2006). The roots with root nodules were separated
rom the shoot at the stem base, immediately put into tightly sealedest vials (2000 ml), and purified C2H2 was injected to obtain ancetylene concentration of 10% (v/v) in the gas phase (air). Aftern hour, 1 ml of the gas phase was taken from the inside of testessels with a Hamilton gas-tight syringe and stored in small glassials, which were sealed with rubber septa and aluminium seals.thylene concentration was determined using gas chromatographHROM 5 (Laboratorni Pristroje, Praha, Czech Republic). The activ-
ty of dinitrogenase was determined on the basis of the quantity ofcetylene reduced to ethylene and expressed in nmol C2H4 pro-uced per hour per gram of dry weight of root nodules (nmol2H4 h−1 g−1 of nodules).
.5. Enumeration of selected soil microorganisms
Soil microorganisms were counted by the dilution plate methodccording to Koch (Rodina, 1968) on adequate agar substrate (inve replications) and expressed in colony-forming units (cfu) g−1
W of soil. Oligotrophic and copiotrophic microorganisms wereetermined according to Hattori and Hattori (1980) and the platesere incubated at 28 ◦C for 14 and 7 days, respectively. The number
f actinobacteria was assessed on Pochon medium after 5 days ofncubation at 24 ◦C (Grabinska-Łoniewska, 1999).
.6. Soil enzymatic activity
Biochemical analyses of soil involved the determination ofctivities of acid (EC 3.1.3.1.) and alkaline (EC 3.1.3.2.) phospho-onoesterases by the method of Tabatabai and Bremner (1969).
he activities were determined using as substrate disodium p-itrophenyl phosphate tetrahydrate, after 1-h incubation at 37 ◦Ct a wavelength of 400 nm. Results were converted into �g p-itrophenol (p-NP) h−1 g−1 DW of soil.
tPbt
ngineering 58 (2013) 214– 227 217
.7. Phenolic compounds in soil
Concentration of total water-soluble phenolics in soil wasssessed using a slightly modified method of Muscolo and Sidari1998). Phenols were extracted with distilled water from dried andieved soil, at a ratio of 1:10 (w/v). Using the colour reaction ofhenols in Na2CO3 with Folin–Ciocalteau’s reagent, we assayed theoncentration of phenolic compounds spectrophotometrically at aavelength of 750 nm. Tannic acid (TAE) was used as a standard.
otal water-soluble phenolic concentrations were expressed asannic acid equivalents (�g TAE g−1 DW of soil).
.8. Statistical analysis and data treatment
The experiment was set up in a completely randomized designith 12 replicate plants for each alder species, seedling origin and
reatment for morphological, elemental and nitrogen fixation anal-ses. Soil samples from each pot were taken for microbiological,nzymatic and phenolic determinations immediately after plantarvesting. The tolerance index (%) was calculated by dividingean root weight of the seedlings grown in polluted soil (xf ) byean root weight of the seedlings grown in control soil (xc), i.e.
I (%) = xf
xc× 100
The standard error (SE) of the tolerance index was calculatedccording to the formula
E (%) =
√(1xc
)2s2
f+
(xf
x2c
)2
s2c × 100
here s is the standard error of the mean, c is the control, and f ishe polluted soil.
The above formula was derived from the error propagation lawBrandt, 1970)
2(yi) =n∑
j=1
(∂yi
∂xj
)2
�2(xj)
All results are presented as mean values with standard error±SE). Data were analyzed using STATISTICA 5.1 (StatSoft Inc., USA).
eans were compared by using the Fisher’s least significant dif-erence (LSD) test, with the exception of the data pertaining toolerance index. In the last case, results were compared on theasis of standard errors (Brandt, 1970). Differences were consid-red significant at p ≤ 0.05. Two-way analysis of variance (ANOVA)as used to examine the significance of factors: alder species,rovenances and treatment (control vs. polluted soil) and their
nteractions.
. Results and discussion
.1. Soil pollution
In the area of 2840 ha of the buffer zone of the “Głogów” Coppermelter, soil moisture content and pH as well as concentrations ofomponents of the soil solution (macro- and micronutrients) varyreatly, except for Cu and Pb, whose critical concentrations, 125 mgu kg−1 and 400 mg Pb kg−1 (Alloway, 1995) are always exceeded
n soil collected at the depth of 5–20 cm in various locations within
he buffer zone (Stefanowicz et al., 2009; Stobrawa and Lorenc-lucinska, 2008). In our study, metal concentrations in soil from theuffer zone of the same copper smelter (but in different locationshan in the cited works) were 12-fold higher for Cu and 1.2-fold
218G
. Lorenc-Plucinska
et al.
/ Ecological
Engineering 58 (2013) 214– 227
Table 3Concentrations of elements (N and S in %, others in mg kg−1 DW) in roots of Alnus incana and A. glutinosa seedlings from 3 provenances (Kr, Rp and Wl), grown in unpolluted (control) and polluted soil.
Element Alnus incana Alnus glutinosa
Kr Rp Wl Kr Rp Wl
Control Polluted Control Polluted Control Polluted Control Polluted Control Polluted Control Polluted
N 1.37 ± 0.02 1.42 ± 0.03 1.444 ± 0.005 1.49 ± 0.02 1.18 ± 0.04 1.46 ± 0.04** 1.37 ± 0.04 1.37 ± 0.05 1.48 ± 0.01 1.25 ± 0.04** 1.17 ± 0.05 1.29 ± 0.03P 972 ± 46 951 ± 20 799 ± 47 889 ± 54 982 ± 111 876 ± 17 1264 ± 83 804 ± 16*** 789 ± 21 633 ± 30** 1146 ± 100 632 ± 11***
K 3412 ± 44 4446 ± 129*** 3033 ± 261 2531 ± 62 4134 ± 129 3990 ± 65 4813 ± 333 4200 ± 236 2809 ± 90 3065 ± 118 4126 ± 317 3074 ± 169S 0.10 ± 0.01 0.102 ± 0.004 0.1 ± 0.01 0.091 ± 0.003 0.074 ± 0.003 0.09 ± 0.005 0.076 ± 0.003 0.18 ± 0.02** 0.1 ± 0.01 0.14 ± 0.01 0.08 ± 0.005 0.154 ± 0.01***
Mg 2348 ± 82 2067 ± 82* 2065 ± 106 1533 ± 48*** 2260 ± 75 1749 ± 68*** 2454 ± 20 1951 ± 32**** 2271 ± 138 1964 ± 52* 2179 ± 159 1967 ± 56*
Ca 16,828 ± 399 7889 ± 195**** 11,213 ± 601 7757 ± 215**** 15,663 ± 731 7761 ± 252**** 15,650 ± 1097 8692 ± 202**** 12,540 ± 804 9111 ± 165** 17,698 ± 779 8804 ± 182****
Fe 2233 ± 128 1539 ± 110*** 2410 ± 27 1608 ± 98*** 2487 ± 223 1267 ± 56**** 3580 ± 433 2055 ± 52** 2814 ± 98 1594 ± 78**** 2881 ± 186 1754 ± 174***
Cu 13.46 ± 0.97 3972 ± 302**** 10.6 ± 0.6 2628 ± 108**** 11.9 ± 1 3813 ± 376**** 10.96 ± 0.2 3638 ± 299**** 33.5 ± 5.7 3599 ± 255**** 14.5 ± 0.6 3359 ± 186****
Zn 25.4 ± 3.4 62.7 ± 3.2**** 31 ± 1 57 ± 3**** 28.3 ± 0.9 69.7 ± 2.1**** 34.5 ± 1.9 76.6 ± 1.5**** 32 ± 3 71.2 ± 3.9**** 31.6 ± 3.1 57.3 ± 2.1****
Cd 0.4 ± 0.01 1.19 ± 0.09**** 0.245 ± 0.007 0.82 ± 0.04**** 0.37 ± 0.03 0.98 ± 0.04**** 0.62 ± 0.04 1.41 ± 0.05**** 0.38 ± 0.02 1.06 ± 0.06**** 0.39 ± 0.03 1.12 ± 0.07****
Pb 2.9 ± 0.5 245 ± 17**** 1.47 ± 0.42 173 ± 12**** 2.19 ± 0.08 236 ± 23**** 3.51 ± 0.27 213 ± 13**** 1.93 ± 0.23 198 ± 12**** 2.96 ± 0.22 215 ± 15****
Mean values ± SE of 12 random samples.Significant differences from the control:
* p < 0.05.** p < 0.01.
*** p < 0.001.**** p < 0.0001.
Table 4Concentrations of elements (N in %; others in mg kg−1 DW) in stems of Alnus incana and A. glutinosa seedlings from 3 provenances (Kr, Rp and Wl), grown in unpolluted (control) and polluted soil.
Element Alnus incana Alnus glutinosa
Kr Rp Wl Kr Rp Wl
Control Polluted Control Polluted Control Polluted Control Polluted Control Polluted Control Polluted
N 0.79 ± 0.03 0.79 ± 0.01 0.97 ± 0.01 0.88 ± 0.03 0.82 ± 0.01 0.80 ± 0.01 0.99 ± 0.03 0.87 ± 0.01** 0.86 ± 0.01 0.80 ± 0.01 0.84 ± 0.01 0.76 ± 0.03*
P 459 ± 27 569 ± 17* 493 ± 28 535 ± 49 427 ± 30 557 ± 18** 745 ± 29 452 ± 24**** 478 ± 17 302 ± 12*** 589 ± 17 340 ± 15***
K 2529 ± 97 2692 ± 77 2979 ± 89 2678 ± 197 2430 ± 132 2686 ± 119 3445 ± 177 4009 ± 193 3449 ± 161 3131 ± 203 3402 ± 89 3201 ± 144Mg 672 ± 6 873 ± 13*** 751 ± 25 872 ± 11** 645 ± 20 700 ± 15 929 ± 75 1047 ± 72 725 ± 40 841 ± 26* 729 ± 41 1070 ± 18***
Ca 5980 ± 231 4981 ± 190** 5105 ± 224 4611 ± 205 5353 ± 299 4262 ± 142** 7221 ± 417 4466 ± 113*** 6755 ± 332 4295 ± 183*** 6571 ± 461 4551 ± 222**
Fe 23 ± 2 26 ± 2 32 ± 3 29 ± 1 38 ± 2 36 ± 1 53 ± 4 50 ± 8 26 ± 3 18 ± 1 21 ± 5 25 ± 2Cu 3.4 ± 0.5 7.5 ± 0.3**** 1.8 ± 0.1 5.7 ± 0.1**** 2.45 ± 0.06 6 ± 0.4**** 2.56 ± 0.09 9.98 ± 0.63**** 1.69 ± 0.06 7.3 ± 0.2**** 2.59 ± 0.08 16 ± 1****
Zn 25 ± 3 37 ± 1* 28 ± 3 29 ± 3 27 ± 1 38 ± 1** 24 ± 1 30 ± 2* 21 ± 2 19 ± 1 17 ± 1 19.3 ± 0.9Cd 0.036 ± 0.002 0.072 ± 0.003**** 0.024 ± 0.001 0.048 ± 0.003**** 0.027 ± 0.003 0.044 ± 0.003** 0.054 ± 0.003 0.059 ± 0.005 0.04 ± 0.01 0.03 ± 0.002) 0.024 ± 0.003 0.028 ± 0.003Pb 0.055 ± 0.003 0.38 ± 0.1**** 0.07 ± 0.01 0.27 ± 0.02**** 0.07 ± 0.01 0.26 ± 0.01**** 0.092 ± 0.002 0.47 ± 0.02**** 0.17 ± 0.04 0.36 ± 0.02** 0.08 ± 0.01 0.68 ± 0.06****
Mean values ± SE of 12 random samples.Significant differences from the control:
* p < 0.05.** p < 0.01.
*** p < 0.001.**** p < 0.0001.
gical Engineering 58 (2013) 214– 227 219
hatltb3
(p2f
atbfsPooNNtidv
3
CirCaSaif
orfPdCPhCt
atlsami
3
(i
ns
of
elem
ents
(N
and
S
in
%;
oth
ers
in
mg
kg−1
DW
)
in
leav
es
of
Aln
us
inca
na
and
A. g
luti
nosa
seed
lin
gs
from
3
pro
ven
ance
s
(Kr,
Rp
and
Wl)
, gro
wn
in
un
pol
lute
d
(con
trol
)
and
pol
lute
d
soil
.
lnus
inca
na
Aln
us
glut
inos
a
r
Rp
Wl
Kr
Rp
Wl
ontr
ol
Poll
ute
d
Con
trol
Poll
ute
d
Con
trol
Poll
ute
d
Con
trol
Poll
ute
d
Con
trol
Poll
ute
d
Con
trol
Poll
ute
d
2.3
±
0.2
1.82
±
0.04
*2.
23
±
0.05
1.88
±
0.02
***
2.2
±
0.1
1.73
±
0.11
*2.
3
±
0.1
1.73
±
0.02
****
2.4
±
0.1
2.16
±
0.1
2.51
±
0.06
1.95
±
0.03
****
998
±
15
1031
±
17
930
±
42
1129
±
132
942
±
27
873
± 52
1159
±
61
925
±
36**
1089
±
26
948
±
29**
1098
±
58
866
±
18**
1,46
9
±
740
15,7
86
±
230**
**13
,461
±
493
12,5
71
±
805
9394
±
224
12,2
70
± 68
7**15
,366
±
271
12,9
32
±
801*
11,2
04
±
667
12,4
81
±
870
11,2
61
±
571
9609
±
663
0.13
±
0.01
0.11
±
0.00
3*0.
139
±
0.01
0.11
3
±
0.00
3**0.
126
±
0.01
0.10
3 ±
0.01
*0.
108
±
0.00
3
0.15
±
0.01
**0.
144
±
0.01
0.14
3
±
0.01
0.11
4
±
0.00
2
0.16
7
±
0.00
4****
3166
±
9445
54
±
46**
**34
58
±
337
5953
±
332**
*32
86
±
61
4073
±
45**
**43
29
±
102
4764
±
124*
3537
±
221
4892
±
248**
3191
±
105
6918
±
486**
**
1,32
9
±
843
22,9
19
±
481
22,3
15
±
890
19,8
03
±
371
17,8
50
±
331
19,0
33
±
335
22,7
78
±
599
14,5
58
±
421**
**17
,833
±
639
16,1
03
±
363*
22,0
61
±
1006
17,2
44
±
1328
*
97
±
6
97
±
5
93
±
5
146
±
6***
96
±
2
85
±
5*17
0
±
11
147
±
13
168
±
4
105
±
4****
100
±
4
136
±
9**
4.4
±
0.3
19
±
1****
4.6
±
0.6
16
±
0.8**
**4.
9
± 0.
211
.0
±
0.1**
**6.
9
±
0.7
15.1
±
0.6**
**7.
4
±
0.2
19
±
3***
5.9
±
0.2
15.4
±
0.6**
**
30
±
3
61
±
3****
21
±
2
39
±
3***
29
± 3
60
±
4****
27
±
3
48
±
5**23
.5
±
1
39.2
±
0.8**
**19
.2
±
0.9
45
±
2****
0.02
6
±
0.00
20.
057
±
0.01
**0.
027
±
0.00
20.
027
±
0.00
2
0.01
7 ±
0.00
2
0.03
4
±
0.00
3***
0.04
8
±
0.01
0.04
9
±
0.00
4
0.03
8
±
0.00
4
0.04
1
±
0.00
4
0.01
8
±
0.00
2
0.02
3
±
0.00
20.
279
±
0.01
0.64
±
0.04
****
0.43
±
0.07
0.58
±
0.07
**0.
397
±
0.00
3
0.49
±
0.03
**0.
92
±
0.1
1.1
±
0.06
0.63
±
0.02
0.79
±
0.1*
0.67
±
0.02
1.23
±
0.02
****
±
SE
of
12
ran
dom
sam
ple
s.ff
eren
ces
from
the
con
trol
:
. 1.
G. Lorenc-Plucinska et al. / Ecolo
igher for Pb than the upper limit of total critical levels (Table 2)nd were in the phytotoxic range (Alloway, 1995). Also concen-rations of bioavailable forms of Cu and Pb exceeded regulatoryevels (<100 mg kg−1) according to Polish legislation (Regulation ofhe Ministry of Environment, 2002). In the soil collected from theuffer zone, their concentrations were 756-fold higher for Cu and2-fold higher for Pb than in the control forest soil.
Total concentrations of Fe, Zn, Mn, Cr and Cd in polluted soilTable 2) were close to the upper limit of permissible levels forostagricultural or afforested lands (Kabata-Pendias and Pendias,001), although they were 1.4-fold higher for Fe, 2.9-fold for Zn, 2.5-old for Mn and Cr, and 1.2-fold for Cd than in the control (Table 2).
In comparison with unpolluted soil (control), polluted soil waslso characterized by lower pH (5.92 vs. 7.01) and higher concen-rations of K, Mg and S, while concentrations of Ca, P, C, N and itsioavailable forms (N-NH4, N-NO3) were lower than in the controlorest soil (Table 2). Similar relationships were observed in othertudies of the copper smelter buffer zone (Stobrawa and Lorenc-lucinska, 2008). Generally it is assumed that both mineral formsf nitrogen (N-NH4, N-NO3) account for about 1–5% of total N. Inur study the relationship is preserved in the control (N-NH4, N-O3 ≈ 2.5% of total N) and markedly reduced in polluted soil, where-NH4 and N-NO3 account for only 0.22% of total N. Special atten-
ion should be paid to the low organic matter content and C:N ration polluted soil (Table 2), lower than the values reported for soils ofeciduous forest and farmlands (Demoling et al., 2007). Such lowalues are usually found in most degraded soils (Wong, 2003).
.2. Influence of polluted soil on element concentrations in roots
Both alder species, when grown in polluted soil, accumulatedu (A. incana ≈ A. glutinosa, p > 0.05) and stored Cd (A. glutinosa > A.
ncana, p = 0.002), Pb and Zn (A. incana ≈ A. glutinosa, p > 0.05) inoots (Table 3). Critical levels in plants, i.e. 20–100 mg kg−1 DW foru and 30–300 mg kg−1 DW for Pb (Alloway, 1995; Kabata-Pendiasnd Pendias, 2001), were exceeded in roots of both alder species.eedlings of A. incana with higher initial root biomass (Table 1)ccumulated in their roots lower concentrations of trace elements,ncluding Cu, Zn, Cd and Pb. No such a relationship was observedor A. glutinosa (Table 3).
The accumulation of Cu and storage of Zn, Cd and Pb in rootsf both alder species exceeded concentrations of these metalsecorded earlier for Populus nigra seedlings, also grown in soilrom the buffer zone of a copper smelter (Stobrawa and Lorenc-lucinska, 2008). Even in fine roots of 26-year-old P. nigra and P.eltoides trees growing in the buffer zone of the copper smelter,u, Pb and Cd concentrations were lower (Stobrawa and Lorenc-lucinska, 2007). These results clearly indicate an exceptionallyigh capacity for and efficiency of the uptake and storage of Cu,d, Pb and Zn by alder roots, or their inability to exclude them inhese conditions.
Concentrations of Fe and Ca in fine roots of both Alnus speciesnd P in A. glutinosa grown in polluted soil were lower than inhe control (Table 3), while concentrations of Ca in the soil wereower and Fetotal, Feavailable and Pavailable were higher in pollutedoil (Table 2). This could result from reduction of the uptake of Fend P by Cu (Ke et al., 2007). Alder growth in polluted soil witharkedly higher concentrations of Stotal and Savailable also led to
ncreased concentrations of S in roots of A. glutinosa (Table 3).
.3. Influence of polluted soil on element concentrations in shoots
Concentrations of Cu, Zn, Cd and Pb in above-ground shootsi.e. leaves and stems) of both alder species were lower thann roots (Tables 4 and 5). The efficiency of metal uptake and Ta
ble
5C
once
ntr
atio
Elem
ent
A K C
N
P K
1S M
g
Ca
2Fe
Cu
Zn
Cd
Pb
Mea
n
valu
esSi
gnifi
can
t
di
*p
<
0.05
.**
p
<
0.01
.**
*p
<
0.00
1**
**p
<
0.00
0
220 G. Lorenc-Plucinska et al. / Ecological Engineering 58 (2013) 214– 227
F Ai) ans ificant
t(mPtv2>mmepPaSoeemfms(
lpo2C(esa
amPfg
uca(rawai
i(attaosirionpMo
rtc(aPp
ig. 1. Bioconcentration factors (BCF) of Zn, Cd, Cu and Pb in shoots of Alnus incana (oil. Mean values ± SE of 12 random samples; different letters (a, b, c) indicate sign
ransfer is reflected in values of bioconcentration factorsBCFshoots), dependent on plant species and its tolerance to trace
etals and their concentrations in soil (Jeyakumar et al., 2010;ourrut et al., 2011). It is assumed that in plants suitable for phy-oextraction, values of BCFshoots for a given metal are >1, whilealues <1 indicate usefulness for phytostabilization (Bech et al.,012; Pourrut et al., 2011). In this study, only BCFshoots for Zn was1 (A. incana > A. glutinosa, p = 0.021) (Fig. 1), which confirms a highobility and transfer of Zn from roots to shoots and Zn bioaccu-ulation, frequently observed also in other tree species (Jeyakumar
t al., 2010). By contrast, BCFshoots < 1 for Cd (A. incana ≈ A. glutinosa, > 0.05) and especially for Cu (A. incana < A. glutinosa, p = 0.036) andb (A. incana < A. glutinosa, p = 0.001), indicate low transfer of Cd, Cund Pb to shoots and accumulation of these trace metals in roots.imilar relationships, namely BCFshoots < 1 for Cd, Cu and Pb, werebserved in A. incana (Rosselli et al., 2003) and A. glutinosa (Pourrutt al., 2011) growing in soil polluted with Cu, Zn, Cd and Pb. Rossellit al. (2003) recommend Alnus as metal excluders, able to stabilizeetal in the rhizosphere and thus to avoid its uptake or exclusion
rom above-ground parts through negligible transfer of toxic traceetals from roots. The latter possibility is confirmed in both alder
pecies grown in polluted soil from the copper smelter buffer zoneTables 4 and 5).
Concentrations of Cu, Zn, Cd and Pb in alder leaves grown in pol-uted soil were within normal ranges reported for leaves of variouslant species (Kabata-Pendias and Pendias, 2001) and for leavesf A. glutinosa growing on uncontaminated soils (Pourrut et al.,011; Vandecasteele et al., 2008). Although concentrations of Zn,u and Pb in leaves of both alder species were higher than in stemsTables 4 and 5), the risk of spreading these trace metals in thenvironment and their redistribution and release of metals to theoil (Castiglione et al., 2009; Scheid et al., 2009) seems to be low inlders growing in soil from the buffer zone of the copper smelter.
The foliar concentrations of N, K, S, Mg and Ca in A. incanand A. glutinosa grown in forest soil (control) were within nor-
al ranges for plants (Marschner, 1995), while concentrations of(0.09–0.12%) (Table 5) were markedly lower than those reportedor various plant species (0.3–0.5%) (Marschner, 1995), including A.lutinosa (0.22–0.26%) (Vandecasteele et al., 2008). Alder leaves are
3
e
d A. glutinosa (Ag) seedlings from 3 provenances (Kr, Rp and Wl), grown in polluted differences (LSD-test, p ≤ 0.05).
sually rich in N (Kuznetsova et al., 2010, 2011), as its concentrationan reach 3.2–3.6% (Vandecasteele et al., 2008). N concentration inlder leaves from polluted soil (A. incana < A. glutinosa, p = 0.004)Table 5) was lower than in the control and was not only below theanges estimated for A. glutinosa (Vandecasteele et al., 2008), butlso for other plant species (2–5%) (Marschner, 1995). Moreover,e recorded decreased concentrations of P and Ca in A. glutinosa
nd of S in A. incana, while an increase in S in A. glutinosa and in Mgn both species (A. glutinosa ≈ A. incana, p = 0.05) (Table 5).
At optimal steady state for nutrition and maximum growth of A.ncana, nutrient weight proportions P:K:Ca:Mg are about 18:50:5:9Ingestad, 1987). In our study only values of the K:N ratio of bothlder species from the control forest soil corresponded to Inges-ad’s ratios. By contrast, the P:N ratio was ca. 4.1-fold lower thanhe respective optimum value, while the Ca:N was 17.4-fold highernd Mg:N was 2.4-fold higher (Table 6). Interestingly, similar valuesf P:K:Ca:Mg ratios for leaves of A. incana and A. glutinosa indicatedimilarity in nutrient proportion requirements between the stud-ed alder species. The differences between Ingestad’s P:K:Ca:Mgatio and that recorded in our study could result from differencesn pH and concentrations of the analyzed elements present in vari-us compounds in forest soil, as both the factors affect solubility ofutrients in the soil solution and thus their bioavailability. As com-ared with Ingestad’s ratios, lower P:N ratio and higher Ca:N andg:N ratios were recorded also in leaves of A. glutinosa growing in
il-shale mining areas (Kuznetsova et al., 2010).The P:K:Ca:Mg ratios for leaves of A. incana and K:N and Mg:N
atios for leaves of A. glutinosa grown in polluted soil were higherhan in the control (Table 6). These differences in observationsould be the result of lower N concentrations in polluted soilTable 2) and lower N concentrations in leaves (Table 5) as wells the possible antagonism between Cu and N (Kabata-Pendias andendias, 2001), and thus disturbances in mineral composition oflants (Ke et al., 2007).
.4. Influence of polluted soil on seedling growth and biomass
After 158 days of growth, alder leaf biomass was reduced,specially in A. incana originating from Kr (ca. 38%, p < 0.001)
G. Lorenc-Plucinska et al. / Ecological Engineering 58 (2013) 214– 227 221
Table 6Nutrient weight proportions (N = 100) for P, K, Ca and Mg in leaves of Alnus incana and A. glutinosa seedlings grown in unpolluted (control) and polluted soil.
Species Soil P:N K:N Ca:N Mg:N
Alnus incana Control 4.5 ± 0.2(a) 53 ± 3(a) 94 ± 4(a) 14.9 ± 0.7(a)Polluted 5.5 ± 0.3(b) 75 ± 3(b) 114 ± 3(b) 27 ± 1(b)
Alnus glutinosa Control 4.8 ± 0.2(a) 53 ± 3(a) 89 ± 4(a) 15.6 ± 0.7(a)
D < 0.05
(aoamflc
cp2
FCi
Polluted 4.9 ± 0.2(a)
ifferent letters (a, b, c) within columns indicate significant differences (LSD-test, p
Fig. 2). Leaf biomass production depends on the ability tobsorb solar energy and use it for growth and developmentf vegetative tissues, but also on adequate supply of nutrients
nd water (Demura and Ye, 2010). There are many reports onultidirectional disturbances in pigment synthesis, chlorophylluorescence, electron transport, gas exchange, activity of Calvinycle enzymes, and transport of assimilates due to excessive
ile(
ig. 2. Biomass, shoot/root ratios and tolerance index of Alnus incana (Ai) and A. glutinosaS) and polluted soil (PS). Mean values ± SE of 12 random samples. Significant differences
ndex differ significantly (p < 0.05).
62 ± 4(a) 84 ± 3(a) 30 ± 2(b)
).
oncentrations of Cu, Zn, Pb or Cd added in defined doses tootting soil or being components of polluted soil (Borghi et al.,008; Gaudet et al., 2011). Thus it is highly probable that sim-
lar disturbances could also contribute to the decrease in aldereaf biomass in this study. We also cannot exclude a negativeffect of disturbances in macronutrient distribution and utilizationTable 5) on photosynthetic activity, metabolic processes and leaf
(Ag) seedlings from 3 provenances (Kr, Rp and Wl), grown in control (unpolluted,from the control: *p < 0.05; **p < 0.01; ***p < 0.001. Different letters for the tolerance
2 gical Engineering 58 (2013) 214– 227
b2
o(aKscootetptfsvs2tc
3c
tlgnocr2
gmantAnAZi
oca(2l(sap
lweecw
ns
of
elem
ents
(N
in
%;
oth
ers
in
mg
kg−1
DW
)
in
root
nod
ule
s
of
Aln
us
inca
na
and
A. g
luti
nosa
seed
lin
gs
from
3
pro
ven
ance
s (K
r,
Rp
and
Wl)
, gro
wn
in
un
pol
lute
d
(con
trol
)
and
pol
lute
d
soil
.
Aln
us
inca
naA
lnus
glut
inos
a
Kr
Rp
Wl
Kr
Rp
Wl
Con
trol
Poll
ute
d
Con
trol
Poll
ute
d
Con
trol
Poll
ute
d
Con
trol
Poll
ute
d
Con
trol
Poll
ute
d
Con
trol
Poll
ute
d
2.7
±
0.2
2.33
±
0.11
2.36
±
0.15
2.1
±
0.2
2.18
±
0.15
2.11
±
0.2
2.7
±
0.2
2.21
±
0.13
*2.
54
±
0.28
2.16
±
0.29
2.46
±
0.19
2.05
±
0.14
1088
±
1510
12
±
9*12
14
±
2410
60
±
10**
1144
±
22
847
± 10
***
1063
±
15
1084
±
19
1310
±
15
1253
±
8*10
88
±
10
1033
±
5**
3692
±
49
3004
±
49**
*39
51
±
130
2901
±
45**
3707
±
91
2954
± 90
**34
38
±
53
4626
±
27**
**32
03
±
72
4247
±
37**
*32
63
±
84
4214
±
44**
*
2140
±
4
1956
±
5****
2194
±
30
1674
±
5****
1974
±
29
1536
± 8**
*11
05
±
10
1302
±
13**
*14
97
±
5
1804
±
5****
1323
±
18
1537
±
11**
*
12,6
76
±
72
8841
±
89**
**14
,591
±
236
8239
±
27**
**13
,265
±
222
7211
±
102**
**68
78
±
157
3239
±
74**
**98
78
±
69
5932
±
93**
**86
16
±
50
4819
±
54**
**
726
±
4
1356
±
6****
1118
±
6
1699
±
7****
1308
±
24
1692
±
20**
*11
19
±
9
1293
±
17**
1589
±
14
1626
±
16
1083
±
4
1649
±
7****
8.3
±
0.3
813
±
4****
7.2
±
0.1
866
±
3****
6.4
±
0.2
670
±
4****
7.9
±
0.1
508
±
5****
8.4
±
0.3
686
±
4****
7.45
±
0.07
693
±
2****
18.8
±
0.4
27.8
±
0.3**
**32
.5
±
0.2
40.5
±
0.2**
**19
.9
± 0.
1 29
.84
±
0.05
****
32.0
6
±
0.04
41.3
±
0.7**
*45
.19
±
0.01
53.6
±
0.2**
**31
.9
±
0.2
40.6
±
0.1**
**
0.25
±
0.01
0.52
±
0.02
***
0.26
±
0.01
0.48
±
0.02
***
0.14
± 0.
01
0.38
2
±
0.00
7***
0.2
±
0.01
0.32
±
0.01
***
0.23
5
±
0.01
0.39
3
±
0.00
8***
0.17
±
0.02
0.39
1
±
0.00
6***
1.64
±
0.02
61
±
0.3**
**3.
1
±
0.01
70.3
±
0.2**
**3.
1 ±
0.1
56.1
±
0.2**
**2.
52
±
0.02
46.1
±
0.1**
**4.
26
±
0.01
68.3
9
±
0.03
****
3.26
±
0.01
68.5
8
±
0.05
****
±
SE
of
12
ran
dom
sam
ple
s.ff
eren
ces
from
the
con
trol
:
. 1.
22 G. Lorenc-Plucinska et al. / Ecolo
iomass production (Amtmann and Armengaud, 2009; Liu et al.,009).
We did not record any negative effect of growth in polluted soiln the biomass of stems, roots, nodules, and total seedling biomassleaves + stems + roots) of both alder species originating from Rpnd Wl, and of A. glutinosa from Kr, while A. incana originating fromr was distinguished by a strong reduction of biomass (Fig. 2). Initialeedling height and biomass in A. incana from Kr (Table 1), like con-entrations of harmful trace metals and major nutrients in seedlingrgans after the experiment, did not differ significantly from thethers (Tables 3 and 4), which attests to similarity in efficiency ofheir uptake and translocation. It therefore appears that the low-red seedling biomass in A. incana originating from Kr results fromhe plants’ lower ability to cope with unfavourable conditions ofolluted soil (toxic metals as well as disturbances in concentra-ions and bioavailability of nutrients). Tolerance index for A. incanarom Kr reached (x ± SE) 81.3 ± 0.1% and was lower than in othereedlings, where it reached 91–105% (Fig. 2). High tolerance indexalues for alder exceeded earlier reported values for various treepecies growing in soil polluted with Cu, Zn, Cd or Pb (Borghi et al.,008; Shi et al., 2011; Shu et al., 2012), where accumulation ofrace metals in roots led to reduction of biomass and morphometrichanges in roots (Borghi et al., 2008; Shi et al., 2011).
.5. Influence of polluted soil on root nodules: elementoncentrations, biomass and nitrogen fixation
Alder growth in polluted soil led to increased concentrations ofrace metals, mostly of Cu (A. incana > A. glutinosa, p = 0.002), fol-owed by Pb (A. incana ≈ A. glutinosa, p > 0.05), Zn (A. incana < A.lutinosa, p = 0.001) and Cd (A. incana > A. glutinosa, p = 0.002) in rootodules (Table 7). Concentrations of Cu, Zn and Pb for A. incana andf Zn for A. glutinosa were higher in nodules of seedlings from Rp, inomparison with those from Kr and Wl. Concentrations in seedlingoots were higher than in nodules: 5-fold for Cu, 3.5-fold for Pb,.5-fold for Cd and 1.5-fold for Zn (Tables 3 and 7).
This is, to our knowledge, the first report showing that in Alnusrowing in polluted soil, Cu, Pb, Zn and Cd are taken up and accu-ulated not only in roots but also in root nodules. According to
vailable literature, Ni accumulation was earlier recorded only inodules of A. glutinosa seedlings treated with various concentra-ions of NiSO4 (Wheeler et al., 2001). We did not investigate if inlnus the toxic trace metals are taken directly from the soil throughodules. It is known, however, that histidine-rich protein nodulinsgNt84 and Ag164, called metallohistins, are able to bind Cu2+,n2+, Cd2+, Ni2+ and Co2+, and by supplying or sequestering of metalons they affect Frankia growth (Gupta et al., 2002).
Seedling growth in polluted soil resulted also in modificationf macronutrient concentrations in nodules. As compared to theontrol, they contained less P and Ca in both alder species as wells less K and Mg in A. incana but more K and Mg in A. glutinosaTable 7). N concentration in nodules of control seedlings reached.49 ± 0.08% (A. incana ≈ A. glutinosa, p > 0.05) and was at a similar
evel as in leaves (Table 5), while nearly 2-fold higher than in rootsTable 3). N concentrations in nodules did not differ between alderpecies (A. incana ≈ A. glutinosa, p > 0.05) grown in polluted soilnd between unpolluted and polluted soil (A. incana ≈ A. glutinosa,
= 0.05) (Table 7).Nodule biomass was similar in seedlings growing in the pol-
uted soil and in the control (A. incana ≈ A. glutinosa, p > 0.05) (Fig. 2),hich suggests that trace metals do not affect nodulation. However,
ffects of the soil environment on nodulation are noticeable (Chaiat al., 2010; Gaulke et al., 2006). In A. crispa a relatively low Cu con-entration of 60 mg kg−1 caused a reduction of nodule dry weight,hile at 100–150 mg kg−1, no nodules were formed and seedling Ta
ble
7C
once
ntr
atio
Elem
ent
N
P K
Mg
Ca
Fe
Cu
Zn
Cd
Pb
Mea
n
valu
esSi
gnifi
can
t
di
*p
<
0.05
.**
p
<
0.01
.**
*p
<
0.00
1**
**p
<
0.00
0
G. Lorenc-Plucinska et al. / Ecological E
Fig. 3. Nitrogen fixation by Frankia measured as acetylene reduction activity (ARA)for root nodules of Alnus incana (Ai) and A. glutinosa (Ag) seedlings from 3 prove-nM*
bTa(nlse
untgftt(ight
(icfrcasg
iaiNcnlGaaocm(
Fb2
astritnecefDr(ir(d
ifpFitawpMMocaar2
3b
aobaoeso(nhnssiw
ances (Kr, Rp and Wl), grown in control (unpolluted, CS) and polluted soil (PS).ean values ± SE of 12 random samples. Significant differences from the control:
p < 0.05; ****p < 0.0001.
iomass declined dramatically (Fessenden and Sutherland, 1979).he lack of biomass reduction in nodules and seedlings of A. incanand A. glutinosa (Fig. 2) at Cu concentrations >1500 mg kg−1 of soilTable 2) may indicate lower sensitivity of A. incana and A. gluti-osa than of A. crispa to high, phytotoxic Cu concentrations. The
ack of effect of high concentrations of Zn, Cd and Pb in biosolids oneedling and nodule biomass was also observed in A. rubra (Gaulket al., 2006).
It must be noted that at the beginning of the experiment, nod-le biomass was similar (A. incana ≈ A. glutinosa, p > 0.05) and didot depend on plant origin (Table 1). By contrast, after 158 days ofhe experiment, polluted soil did not affect nodule biomass in A.lutinosa irrespective of seedling origin, and in A. incana seedlingsrom Rp and Wl, while in A. incana from Kr it was lower than inhe control (Fig. 2). In the last case, it may be yet another symp-om of unusual sensitivity of these particular A. incana seedlingsfrom Kr) to trace metals. It could have resulted from differencesn seed genotypes, provenances, Frankia genotype, and the type ofrowth substrate the used in the nurseries. All these factors mayave played a role in the endpoint performance of these alders inhe trial.
The rate of N2 fixation, measured as acetylene reduction activityARA) for control seedlings of various provenances was nearly evenn A. glutinosa and reached (in nmol C2H4 h−1 g−1 DW of nodules)a. 2400, while in A. incana it ranged between 1500 for seedlingsrom Wl and 5500 for seedlings from Kr (Fig. 3). Nitrogen fixationate indicates fully functional symbiosis of Alnus with Frankia in theontrol. Differences in the rate of N2 fixation between the studiedlder species may result from intrinsic differences between thesepecies, as was reported earlier for alders (A. incana ssp. rugosa > A.lutinosa) in hydroponic conditions (Bélanger et al., 2011).
Alder growth in polluted soil led to a decrease in N2 fixationn nodules of A. incana from Rp and A. glutinosa from Rp and Wl,nd its suppression in both alder species originating from Kr and A.ncana from Wl (Fig. 3). This indicates a decline or suppression of
2 fixation by Frankia. Earlier studies with the use of defined con-entrations of As, Se, V, Cu, Ni or compost and biosolids, reportedo effect of toxic trace metals on alder growth, correlated with a
ack of changes in N2 fixation and nodules (Bélanger et al., 2011;aulke et al., 2006) or the effect of toxic trace metals on nodulectivity was smaller than their effect on the whole plant (Fessendennd Sutherland, 1979; Wheeler et al., 2001). The different effects
n the growth of alder and its symbiotic partner in our researchould be caused by differences between the influence of heavilyetal-polluted soil, poor in organic matter and with a low C:N ratioTable 2) and the influence of a single metal (Bélanger et al., 2011;
wwra
ngineering 58 (2013) 214– 227 223
essenden and Sutherland, 1979; Wheeler et al., 2001) and organiciosolids with high concentrations of Cd, Pb and Zn (Gaulke et al.,006).
The lack of global impact of polluted soil on the biomass oflder seedling organs, including nodules (Fig. 2), associated withuppression of the rate of N2 fixation (Fig. 3), might indicate thathe toxicity of trace metals led to a situation where actinobacteriaeceived photosynthates from the host plant while in turn receiv-ng nitrogen from the symbiont declined severely. It is known thathe presence of root nodules does not necessarily correspond withitrogen fixation ability, as some nodules may be ineffective (Chaiat al., 2010). The presence of functional actinorhizal symbiosis isonnected with an increase in shoot/root biomass ratio (Bélangert al., 2011), since more products of photosynthesis are neededor nodule development and symbiont activity (Persson and Huss-anell, 2009; Roy et al., 2007). In our study shoot/root biomass
atios were similar in alders growing in control and polluted soilFig. 2) with p = 0.757 for the species × provenance × treatmentnteraction. This may indicate that in spite of strongly diminishedate of activity of dinitrogenase for alder grown in polluted soilFig. 3), the symbiont at least partly fulfilled its function, N2 fixationuring the experiment.
Strong decrease in activity of N2-fixing enzyme dinitrogenasen AiPS and AgPS from Kr and AiPS from Wl (Fig. 3) could resultrom sensitivity of Frankia strains to critical levels of trace metals inolluted soil. Richards et al. (2002) found that among 12 comparedrankia strains only 4 were resistant to the activity of 2–20 mM Cu2+
ons (after Roy et al., 2007, i.e. 58–580 mg kg−1), all were resistanto 6–8 mM Pb2+ ions (after Roy et al., 2007, i.e. 164–492 mg kg−1)nd sensitive even to low concentrations (<0.5 mM) of Cd ions,hich led to inhibition of Frankia growth. Dinitrogenase is com-osed of the Fe-protein and the MoFe-protein (Huss-Danell, 1997).o–Cu relations in polluted soil may have antagonistic effects ono uptake by plants and Cu interferes with the enzymatic role
f Mo as a redox carrier (Kabata-Pendias and Pendias, 2001). Thisould be a further explanation for inhibition of the rate of N2 fix-tion in response to high Cu concentrations in polluted soil. Welso cannot exclude the possibility of dinitrogenase inhibition as aesult of reduced synthesis of the enzyme (Mattsson and Sellstedt,002) due to the toxic trace metals.
.6. Counts of actinobacteria, copiotrophic and oligotrophicacteria in the soil
The impact of trace metals on numbers, diversity, biomass, andctivity of soil microorganisms ranges from no effect to decreaser increase. The direction and extent of changes depend on manyiotic and abiotic factors, including toxicity of the given pollut-nt and sensitivity of microorganisms, with the following orderf sensitivity to trace metals: actinobacteria > bacteria > fungi (Gaot al., 2010; He et al., 2010; Jeyakumar et al., 2010). In compari-on with the control forest soil, in metal-polluted soil the countf actinobacteria was reduced after 158 days of alder cultivationFig. 4). The level of reduction depended on alder species (A. gluti-osa > A. incana, p = 0.043) and seedling origin (p = 0.004), and theighest reduction was recorded for seedlings from Rp (Fig. 4). Theumber and development of actinobacteria is strongly affected byoil pH, and most favourable is neutral or alkaline reaction of theoil solution (Golinska and Dahm, 2011). However, it seems thatn our study the major reason of the reduced actinobacteria counts
as not the more acidic pH of polluted soil (5.92) (Table 2), as it
as even higher than pH 4.05–4.16 measured by us in alder standsith abundant actinobacteria (unpublished results). Moreover, aeduced actinobacteria count under the influence of Cd and Pb waslso reported when soil pH reached 8.18 (Gao et al., 2010).
224 G. Lorenc-Plucinska et al. / Ecological Engineering 58 (2013) 214– 227
Fig. 4. Numbers of actinobacteria, copiotrophic and oligotrophic microorganisms, activity of acid (Acid-Pase) and alkaline (Alkali-Pase) phosphomonoesterases, and con-centrations of total water-soluble phenols (SF) in control (unpolluted, CS) and polluted (PS) soil after growth of Alnus incana (Ai) and A. glutinosa (Ag) seedlings from 3provenances (Kr, Rp and Wl). Mean values ± SE of 12 random samples. Significant differences from the control: *p < 0.05; **p < 0.01; ***p < 0.001.
sacAadtglt2ccoatInmioedp
3
eaPAdpthAipotsSu(p
As compared with the control forest soil, in metal-pollutedoil also copiotroph counts were reduced for A. incana from Krnd Wl and A. glutinosa from Rp (Fig. 4). By contrast, oligotrophounts increased (A. incana < A. glutinosa, p = 0.001), especially for. glutinosa from Rp (Fig. 4). Copiotrophic bacteria require a highvailability of organic matter in the soil and in favourable con-itions with rich nutrient resources they may account for 80% ofhe total bacterial count. On the other hand, oligotrophic bacteriarow in nutrient-poor soil with low organic matter content andow C availability (Fierer et al., 2007; Hu et al., 1999). Organic mat-er content and C in polluted soil from the copper smelter was ca..5-fold lower than in the control forest soil (Table 2), which isharacteristic of polluted and degraded soils (Wong, 2003). Thisould be a reason of the observed changes in copiotroph and olig-troph counts. Under stress conditions, with low C resources andvailability and organic reserves, oligotrophs probably are likelyo outcompete copiotrophs (Fierer et al., 2007; Hu et al., 1999).t must be noted that increased or decreased bacterial counts areot necessarily linked with a positive or negative effect of traceetals on functional diversity of bacterial communities and activ-
ty (Becerra-Castro et al., 2012; Kidd et al., 2009). Changes in counts
f actinobacteria, copiotrophs and oligotrophs (Fig. 4) may to somextent result from qualitative and quantitative changes in root exu-ates (Gao et al., 2010; Kidd et al., 2009) of Alnus spp. grown inolluted soil.swpa
.7. Phosphomonoesterase activities in the soil
Both acidic phosphomonoesterases (Acid-Pase) in an acidic soilnvironment and alkaline phosphomonoesterase (Alkali-Pase) inn alkaline soil environment, catalyze the transformation of organic
esters into inorganic P. Plant roots with fungi and bacteria secretecid-Pase, while soil bacteria, fungi, and animals effectively pro-uce Alkali-Pase (Nannipieri et al., 2011). Immediately after theot experiment, the activity of Acid-Pase was nearly 2.3-fold lowerhan that of Alkali-Pase (p < 0.01) in the control forest soil but 2-foldigher in polluted soil (p < 0.001) (Fig. 4). The dramatic inhibition ofcid-Pase (77–86%, p < 0.0001) and Alkali-Pase (95–97%, p < 0.0001)
n polluted soil depended on alder species (A. incana > A. glutinosa, < 0.001). Phosphomonoesterases are metalloenzymes dependentn Ca or Mg. Their modified activity in polluted soil could be dueo formation of complexes of toxic trace metals with enzyme sub-trates and replacement of Ca and Mg by Zn, Cu and Cd (Huang andhindo, 2000; Tabaldi et al., 2007). Acid-Pase activity was lowerednder the influence of an excess of Pb and Cu in fungal exudatesZheng et al., 2009). We also cannot exclude suppression of phos-homonoesterase synthesis by the presence of inorganic P in the
oil (Nannipieri et al., 2011), as its concentrations in polluted soilere higher than in the control forest soil (Table 2). Besides, phos-homonoesterase activity is also strongly affected by the qualitynd quantity of organic matter (Nannipieri et al., 2011), so the
gical E
daltb(
3
ssciDlch(toctie
ciibc2thartan
4
Asalrtn
st2scrrttslaA
Baiho
lKowi
ri(mabcTtht
becaagshfWmdtm2
A
PKUaftKaa
R
A
A
B
G. Lorenc-Plucinska et al. / Ecolo
ifferences in phosphomonoesterase activity in our research couldlso be due to 2-fold lower organic matter content in pol-uted soil than in the control forest soil (Table 2). Moreover,he reduced phosphomonoesterase activity in polluted soil maye a consequence of changes in counts of soil microorganismsFig. 4).
.8. Total water-soluble phenols in the soil
Phenolic compounds in the soil derive mostly from decompo-ition of plant material and, to a lesser extent, from synthesis byoil microbes (Muscolo and Sidari, 1998). In the control forest soilollected in the field before the growing season (early March), thenitial level of total water-soluble phenols (13.9 ± 0.2 �g TAE g−1
W) before planting of alder seedlings was lower than in pol-uted soil (15.1 ± 0.3) (p = 0.009). After the experiment, phenoliconcentrations in the rhizosphere of alder seedlings were 1.2-foldigher in the control (p = 0.005) and 1.7-fold higher in polluted soilp < 0.0001) (Fig. 4) than the initial concentrations. The short dura-ion of the pot experiment and recorded changes in the countsf soil microbes seem to exclude the accumulation of phenolicompounds as a result of organic matter decomposition or syn-hesis by soil microbes. We hypothesize that the observed increasen concentration of total water-soluble phenols results from theirxudation by alder roots.
Phenolic concentrations were higher in polluted soil than in theontrol for both alder species (A. incana < A. glutinosa, p = 0.031),rrespective of their origin (p = 0.075) (Fig. 4). Phenolic componentsn root exudates play an active role in the increase or reduction ofioavailability of nutrients and trace metals, their chelation, pre-ipitation and redox reactions (Degryse et al., 2008; Kidd et al.,009). The high potential of phenolic compounds for metal chela-ion is linked with their antioxidant role. Thanks to the presence ofydroxyl and carboxyl groups, phenols are able to bind metal ionsnd thus to inhibit the superoxide-driven Fenton reaction. Thus inoots of alder seedlings grown in polluted soil, the higher exuda-ion of phenolic compounds may be one of their defence strategiesgainst the toxic trace metals. Its intensity was higher in A. gluti-osa, which is more tolerant to pollution in the soil.
. Conclusions
Our results demonstrate exceptional capabilities of A. incana and. glutinosa to grow in a soil heavily metal-polluted by a coppermelter. After 158 days of growth in polluted soil, the total biomassnd root nodule biomass of Alnus seedlings was similar as in unpol-uted forest soil (control). Both alder species accumulated in theiroots extremely high concentrations of Cu and lower concentra-ions of Pb, Zn and Cd. Accumulation of Cu, Pb, Zn and Cd in rootodules is first reported here.
It has been frequently suggested that alder tolerance to metaltress is based on its tetrapartite symbiosis, especially the mutualis-ic relationship with actinobacteria of the genus Frankia (Roy et al.,007). However, alder growth in the soil collected near the coppermelter led to a considerable decrease in N2 fixation. This indi-ates that the effectiveness of Alnus–Frankia symbiosis could beeduced in highly metal-polluted soil. Also counts of actinobacte-ia and copiotrophic bacteria were greatly reduced, very much likehe activity of Alkali-Pase and, to a lesser extent, of Acid-Pase. Onlyhe count of oligotrophs, abundant under the stress conditions and
hortage of organic reserves, was higher in polluted soil, very muchike exudation of phenolic compounds by alder roots. Nevertheless,ll these changes did not inhibit the increase in seedling biomass in. incana and A. glutinosa and their nodules during the experiment.B
ngineering 58 (2013) 214– 227 225
oth Alnus species, even without the active partnership of Alnusnd Frankia, were able to grow in polluted soil, and high tolerancendex values (81–105%) confirm their exceptional tolerance to theighly unfavourable mineral composition and low organic reservesf the soil near the copper smelter.
Development and tolerance of alder seedlings grown in pol-uted soil depended on their origin. Seedlings of A. incana fromr reached much lower values of biomass and tolerance than thether seedlings. This clearly indicates their lower ability to copeith growth conditions in polluted soil. However, further research
s needed to explain this phenomenon.The growth of both alder species was much better than that
eported earlier for Populus nigra seedlings, which were also grownn a pot experiment with soil from the copper smelter buffer zoneStobrawa and Lorenc-Plucinska, 2008). Moreover, poplars accu-
ulated in their roots less Cu and Pb but more Zn, Cd and Fe thanlders. Also in roots of P. nigra and P. deltoides trees growing in theuffer zone, Cu, Pb and Cd concentrations were lower and Zn con-entrations were higher (Stobrawa and Lorenc-Plucinska, 2007).hese results indicate an exceptionally high ability of Alnus rootso take up and accumulate trace metals, especially Cu and Pb, and aigher tolerance of Alnus to highly metal-polluted soil, as comparedo Populus.
It has been suggested that A. glutinosa is suitable for phytosta-ilization of Cd, Pb and Zn in metal-contaminated soils (Pourrutt al., 2011), while A. incana, for Cu, Zn and Cd from sewage sludgeontaminated compost (Rosselli et al., 2003). In our study, A. incanand A. glutinosa accumulated Cu, Pb, Cd and Zn in roots and nodules,nd transferred only small proportions of Cu, Pb and Cd to above-round parts, including leaves. The results suggest that both thepecies are suitable for phytostabilization of Cu, Pb and Cd in soilseavily polluted by copper smelters. However, our results came
rom short-term pot trials, so the findings require field validation.e cannot exclude that despite normal concentrations of traceetals in alder foliage and the apparent lack of the risk of metal
ispersal, there are potential risks associated with acidification inhe alder rhizosphere and an increase in metal mobility in soil and
etal bioavailability to co-cropped plants (Roy et al., 2007; Wenzel,009).
cknowledgements
This study was supported by the National Centre of Science,oland (grant No. N N305 036340). We would like to thankatarzyna Grewling, Agata Zemleduch-Barylska and Krzysztoffnalski for help in the pot experiment and laboratory work. Welso thank Ewa Maderek, Iwona Pawłowicz and Marcin Kajdaniakor help in the plant trace element analyses. We are grateful tohe staff of “Głogów” Copper Smelter (division of the companyGHM Polska Miedz S.A.) for their kind cooperation. Commentsnd suggestions on this manuscript by two anonymous refereesre appreciated.
eferences
lloway, B.J., 1995. Heavy Metals in Soils, 2nd ed. Blackie Academic & Professional,London, UK.
mtmann, A., Armengaud, P., 2009. Effect of N, P, K and S on metabolism: new knowl-edge gained from multi-level analysis. Curr. Opin. Plant Biol. 12 (3), 275–283.
ecerra-Castro, C., Monterroso, C., Prieto-Fernández, A., Rodríguez-Lamas, L.,Loureiro-Vinas, M., Acea, M.J., Kidd, P.S., 2012. Pseudometallophytes colonis-ing Pb/Zn mine tailings: a description of the plant–microorganism–rhizosphere
soil system and isolation of metal-tolerant bacteria. J. Hazard. Mater. 217-218,350–359.ech, J., Roca, N., Barceló, J., Duran, P., Tume, P., Poschenrieder, C., 2012. Soil andplant contamination by lead mining in Bellmunt (Western Mediterranean Area).J. Geochem. Explor. 113, 94–99.
2 gical E
B
B
B
C
C
C
D
D
D
D
F
F
G
G
G
G
G
G
H
H
H
H
H
H
I
J
K
K
K
K
K
L
L
M
M
M
M
M
N
P
P
P
Q
R
R
R
R
R
S
S
S
S
S
S
T
T
V
26 G. Lorenc-Plucinska et al. / Ecolo
élanger, P.A., Bissonnette, C., Bernèche-D’Amours, A., Bellenger, J.P., Roy, S., 2011.Assessing the adaptability of the actinorhizal symbiosis in the face of environ-mental change. Environ. Exp. Bot. 74, 98–105.
orghi, M., Tognetti, R., Monteforti, G., Sebastiani, L., 2008. Responses of two poplarspecies (Populus alba and Populus × canadensis) to high copper concentrations.Environ. Exp. Bot. 62, 290–299.
randt, S., 1970. Statistical and Computational Methods in Data Analysis. North-Holland Publishing Company, Amsterdam, London.
astiglione, S., Todeschini, V., Franchin, C., Torrigiani, P., Gastaldi, D., Cicatelli, A.,Rinaudo, C., Berta, G., Biondi, S., Lingua, G., 2009. Clonal differences in survivalcapacity, copper and zinc accumulation, and correlation with leaf polyaminelevels in poplar: a large-scale field trial on heavily polluted soil. Environ. Pollut.157 (7), 2017–2108.
haia, E.E., Wall, L.G., Huss-Danell, K., 2010. Life in soil by the actinorhizal root noduleendophyte Frankia. A review. Symbiosis 51 (3), 201–226.
laessens, H., Oosterbaan, A., Savill, P., Rondeux, J., 2010. A review of the charac-teristcs of black alder (Alnus glutinosa (L.) Gaertn.) and their implications forsilvicultural practices. Forestry 83 (2), 163–175.
egryse, F., Verma, V.K., Smolders, E., 2008. Mobilization of Cu and Zn by root exu-dates of dicotyledonous plants in resin-buffered solutions and in soil. Plant Soil306 (1), 69–84.
emoling, F., Figueroa, D., Bååth, E., 2007. Comparison of factor limiting bacterialgrowth in differing soils. Soil Biol. Biochem. 39 (10), 2485–2495.
emura, T., Ye, Z.-H., 2010. Regulation of plant biomass production. Curr. Opin. PlantBiol. 13 (3), 299–304.
ickinson, N.M., 2000. Strategies for sustainable woodland on contaminated soils.Chemosphere 41 (1–2), 259–263.
essenden, R.J., Sutherland, B.J., 1979. The effect of excess soil copper on the growthof black spruce and green alder seedling. Bot. Gaz. 140 (Suppl.), S82–S87.
ierer, N., Bradford, M.A., Jackson, R.B., 2007. Toward an ecological classification ofsoil bacteria. Ecology 88 (6), 1354–1364.
ao, Y., Zhou, P., Mao, L., Zhi, Y., Zhang, C., Shi, W., 2010. Effects of plantspecies coexistence on soil enzyme activities and soil microbial commu-nity structure under Cd and Pb combined pollution. J. Environ. Sci. 22 (7),1040–1048.
audet, M., Pietrini, F., Beritognolo, I., Iori, V., Zacchini, M., Massacci, A., Mugnozza,G.S., Sabatti, M., 2011. Intraspecific variation of physiological and molecu-lar response to cadmium stress in Populus nigra L. Tree Physiol. 31 (12),1309–1318.
aulke, L.S., Henry, C.L., Brown, S.L., 2006. Nitrogen fixation and growth response ofAlnus rubra amended with low and high metal content biosolids. Sci. Agric. 63(4), 351–360.
olinska, P., Dahm, H., 2011. Occurrence of actinomycetes in forest soil. Dendrobi-ology 66, 3–13.
rabinska-Łoniewska, A., 1999. Laboratory classes in general microbiology. OficynaWydaw. Politech., Warszawa (in Polish).
upta, R.K., Dobritsa, S.V., Stiles, C.A., Essington, M.E., Liu, Z., Chen, C.H., Serpersu,E.H., Mullin, B.C., 2002. Metallohistins: a new class of plant metal-binding pro-teins. J. Protein Chem. 21, 529–536.
attori, R., Hattori, T., 1980. Sensitivity to salts and organic compounds of soil bacte-ria isolated on diluted media. J. Gen. Appl. Microbiol. 26 (1), 1–14.
e, L.Y., Zhang, Y.F., Ma, H.Y., Su, L.N., Chen, Z.J., Wang, Q.Y., Qian, M., Sheng, X.F.,2010. Characterization of copper-resistant bacteria and assessment of bacterialcommunities in rhizosphere soils of copper-tolerant plants. Appl. Soil Ecol. 44(1), 49–55.
u, S.J., van Bruggen, A.H.C., Grünwald, N.J., 1999. Dynamics of bacterial populationsin relation to carbon availability in a residue-amended soil. Appl. Soil Ecol. 13(1), 21–30.
uang, Q., Shindo, H., 2000. Effects of copper on the activity and kineticsof free and immobilized acid phosphatase. Soil Biol. Biochem. 32 (13),1885–1892.
uss-Danell, K., 1978. Nitrogenase activity measurements in intact plants of Alnusincana. Physiol. Plant. 43 (4), 372–376.
uss-Danell, K., 1997. Tansley Review No. 93 Actinorhizal symbioses and their N2fixation. New Pytol. 136, 443–445.
ngestad, T., 1987. New concepts on soil fertility and plant nutrition as illustratedby research on forest trees and stands. Geoderma 40 (3–4), 237–252.
eyakumar, P., Loganathan, P., Sivakumaran, S., Anderson, C.W.N., McLaren, R.G.,2010. Bioavailability of copper and zinc to poplar and microorganisms in abiosolids-amended soil. Aust. J. Soil Res. 48 (5), 459–469.
abata-Pendias, A., Pendias, H., 2001. Trace Elements in Soils and Plants, 3rd ed. CRCPress, Boca Raton, USA.
e, W., Xiong, Z.-T., Chen, S., Chen, J., 2007. Effects of copper and mineral on growth,copper accumulation and mineral element uptake in two Rumex japonicuspopulations from a copper mine and an uncontaminated field sites. Environ.Exp. Bot. 59 (1), 59–67.
idd, P., Barceló, J., Pilar Bernal, M., Navari-Izzo, F., Poschenrieder, C., Shilev,S., Clemente, R., Monterroso, C., 2009. Trace element behaviour at theroot–soil interface: implications in phytoremediation. Environ. Exp. Bot. 67 (1),243–259.
uznetsova, T., Lukjanova, A., Mandre, M., Lõhmus, K., 2011. Aboveground biomassand nutrient accumulation dynamics in young black alder, silver birch and Scotspine plantations on reclaimed oil shale mining areas in Estonia. For. Ecol. Man-age. 262 (2), 56–64.
W
ngineering 58 (2013) 214– 227
uznetsova, T., Rosenvald, K., Ostonen, I., Helmisari, H.-S., Mandre, M., Lõhmus, K.,2010. Survival of black alder (Alnus glutinosa L.), silver birch (Betula pendulaRoth.) and Scots pine (Pinus sylvestris L.) seedlings in a reclaimed oil shale miningarea. Ecol. Eng. 36 (4), 495–502.
efranc ois, E., Quoreshi, A., Khasa, D., Fung, M., Whyte, L.G., Roy, S., Greer, C., 2010.Fields performance of adler-Frankia symbionts for the reclamation of oil sandssites. Appl. Soil Ecol. 46 (2), 183–191.
iu, T.Y., Chang, C.Y., Chiou, T.Z., 2009. The long-distance signaling of mineralmacronutrients. Curr. Opin. Plant Biol. 12 (3), 312–319.
arkham, J.H., 2005. The effect of Frankia and Paxillus involutus on the perfor-mance of Alnus incana subsp. rugosa in mine tailings. Can. J. Bot. 83 (11),1384–1390.
arschner, H., 1995. Mineral Nutrition of Higher Plants, 2nd ed. Academic Press,London.
attsson, U., Sellstedt, A., 2002. Nickel affects activity more than expression ofhydrogenase protein in Frankia. Curr. Microbiol. 44 (2), 88–93.
ocek, A., Drzymała, S., 2010. Genesis, Analysis and Soil Classification. Poznan Uni-versity of Life Sciences (in Polish).
uscolo, A., Sidari, M., 1998. Biological activity of humic substances and phenoliccompounds extracted from two different soils of Aspromonte (Southern Italy).Fresen. Environ. Bull. 7, 695–700.
annipieri, P., Giagnoni, L., Landi, L., Renella, G., 2011. Role of phosphatase enzymesin soil. In: Bünemann, E.K., Oberson, A., Frossard, E. (Eds.), Phosphorus in Action.Soil Biology 26. Springer-Verlag, Berlin, Heidelberg, pp. 215–243.
awlowski, K., 2011. Actinorhizal symbioses. In: Polacco, J.C., Todd, C.D. (Eds.),Ecological Aspects of Nitrogen Metabolism in Plants. 1st ed. Willey-Blackwell,Hoboken.
ersson, T., Huss-Danell, K., 2009. Physiology of actinorhizal nodules. In: Pawlowski,K. (Ed.), Prokaryotic Symbionts in Plants. Microbiol. Monogr. 8. Springer-Verlag,Berlin, Heidelberg, pp. 155–178.
ourrut, B., Lopareva-Pohu, A., Pruvot, C., Garc on, G., Veridn, A., Waterlot, C., Bidar,G., Shirali, P., Douay, F., 2011. Assessment of fly ash-aided phytostabilisation ofhighly contaminated soils after an 8-year field trial, Part 2. Influence on plants.Sci. Total Environ. 409 (21), 4504–4510.
uevauviller, P., Rauret, G., Rubio, R., López-Sánchez, J.-F., Ure, J., Bacon, J.,Muntau, H., 1997. Certified reference materials for the quality control ofEDTA- and acetic acid-extractable contents of trace elements in sewagesludge amended soils (CRMs 483 and 484). Fresen. J. Anal. Chem. 357 (6),611–618.
egulation of the Ministry of Environment, 2002. Rozporzadzenie MinistraSrodowiska z dnia 9 wrzesnia 2002 roku w sprawie standardów jakosci glebyoraz standardów jakosci ziemi. Dz. U. Nr 165, poz. 1359 (in Polish).
ichards, J.W., Krumholz, G.D., Chval, M.S., Tisa, L.S., 2002. Heavy metalresistance pattern of Frankia strains. Appl. Environ. Microbiol. 68 (2),923–927.
odina, A., 1968. Microbiological Methods for the Study of Waters. PWRiL,Warszawa (in Polish).
osselli, W., Keller, C., Boschi, K., 2003. Phytoextraction capacity of trees growingon a metal contaminated soil. Plant Soil 256 (2), 265–272.
oy, S., Khasa, D.P., Greer, C.W., 2007. Combining alders, frankiae, and mycorrhizaefor the revegetation and remediation of contaminated ecosystems. Can. J. Bot.85 (3), 237–251.
cheid, S., Günthardt-Goerg, M.S., Schulin, R., Nowack, B., 2009. Accumulation andsolubility of metals during leaf litter decomposition in non-polluted and pol-luted soil. Eur. J. Soil Sci. 60 (4), 613–621.
hi, X., Zhang, X.L., Chen, G.C., Chen, Y.T., Wang, L., Shan, X.Q., 2011. Seedlings growthand metal accumulation of selected woody species in copper and lead/zinc minetailings. J. Environ. Sci. 23 (2), 266–274.
hu, X., Yin, L.Y., Zhang, Q.F., Wang, W., 2012. Effect of Pb toxicity on leaf growth,antioxidant enzyme activities, and photosynthesis in cuttings and seedlings ofJatropha curcas L. Environ. Sci. Pollut. Res. 19 (3), 893–902.
tefanowicz, A.M., Niklinska, M., Laskowski, R., 2009. Pollution-induced toleranceof soil bacterial communities in meadow and forest ecosystems polluted withheavy metals. Eur. J. Soil Biol. 45 (4), 363–369.
tobrawa, K., Lorenc-Plucinska, G., 2008. Thresholds of heavy-metal toxicity incuttings of European black poplar (Populus nigra L.) determined according toantioxidant status of fine roots and morphometrical disorders. Sci. Total Environ.390 (1), 86–96.
tobrawa, K., Lorenc-Plucinska, G., 2007. Changes in antioxidant enzyme activity inthe fine roots of black poplar (Populus nigra L.) and cottonwood (Populus deltoidesBartr. ex Marsch) in a heavy-metal-polluted environment. Plant Soil 298 (1–2),57–68.
abaldi, L.A., Ruppenthal, R., Cargnelutti, D., Morsch, V.M., Pereira, L.B., Schetinger,M.R.C., 2007. Effects of metal elements on acid phosphatase activity in cucumber(Cucumis sativus L.) seedlings. Environ. Exp. Bot. 59 (1), 43–48.
abatabai, M.A., Bremner, J.M., 1969. Use of p-nitrophenyl phosphate for assay ofsoil phosphatase activity. Soil Biol. Biochem. 1 (4), 301–307.
andecasteele, B., Samyn, J., De Vos, B., Muys, B., 2008. Effect of tree species choiceand mineral capping in a woodland phytostabilisation system: a case-study forcalcareous dredged sediment landfills with an oxidised topsoil. Ecol. Eng. 32 (3),
263–273.enzel, W.W., 2009. Rhizosphere processes and management in plant-assisted bioremediation (phytoremediation) of soils. Plant Soil 321 (1–2),385–408.
gical E
W
W
G. Lorenc-Plucinska et al. / Ecolo
heeler, C.T., Hughes, L.T., Oldroyd, J., Pulford, I.D., 2001. Effects of nickel onFrankia and its symbiosis with Alnus glutinosa (L.) Gaertn. Plant Soil. 231 (1),81–90.
hitbread-Abrutat, P.H., 1997. The potential of some soil amendments to improvetree growth on metalliferous mine wastes. Plant Soil 192 (2), 199–217.
W
Z
ngineering 58 (2013) 214– 227 227
ong, M.H., 2003. Ecological restoration of mine degraded soils, with emphasis onmetal contaminated soils. Chemosphere 50 (6), 775–780.
heng, W., Fei, Y., Huang, Y., 2009. Soluble protein and acid phosphatase exudedby ectomycorrhizal fungi and seedlings in response to excessive Cu and Cd. J.Environ. Sci. 21 (12), 1667–1672.
