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ABSTRACTS - WETPOL 2013 - October 13-17, 2013 - Nantes - FRANCE
67
Behaviour of priority and
emerging pollutants in wetlands
ABSTRACTS - WETPOL 2013 - October 13-17, 2013 - Nantes - FRANCE
68
Treatment of Endocrine Disrupting Chemicals (EDCs) by
Constructed Wetlands – A Case Study in Taiwan (O.2)
Lei Yanga, Yi-Peng Jen
b, Ji-Yin Hsieh
c
aDept. of Marine Environment and Engineering, National Sun Yat-sen University, 70 Lien
Hai Road, Kaohsiung, 80424, TAIWAN ([email protected])
bEnvironmental Protection Administration, Executive Yuan, 83 Chung Hua 1st Road, Taipei,
10042, TAIWAN ([email protected])
cDept. of Environmental Science and Engineering, National Pingtung University of Science
and Technology, 1 Shuefu Road, Neipu, Pingtung, 912, TAIWAN
INTRODUCTION
Alkylphenol polyethoxylates (APEOs) have been widely used for industrial, agricultural
and household applications. The biodegradation metabolites of APEOs, such as nonyphenol
and octylphenol, are more persistent and known to disrupt endocrine function in wildlife and
human. These compounds are also recognized as endocrine disrupting chemicals (EDCs).
The objective of this study is to investigate the distribution and removal efficiencies of EDCs,
including nonylphenol diethoxylates, nonylphenol monoethoxylates, nonylphenol, and
octylphenol, for municipal wastewater treated by constructed wetland systems. In addition,
the method of risk quotient was used to evaluate the potential ecological risk of APEOs to
aquatic organisms in wetlands in this study.
METHODS
The research sites included Daniaopi, Hsinhai Bridge I and Hsinhai Bridge II Constructed
Wetlands, all located along the Dahan River in Taipei, Taiwan. The water samples were
taken seasonally from 18 different sampling sites, located in the three construction wetland
systems, separately. The sketch diagram and sampling sites for each constructed wetland
system were shown in Figure 1. The samples were first extracted by using solid-phase
extraction facility (J. T. Baker Ltd.). The extracted samples were then tested for nonylphenol
diethoxylates, nonylphenol monoethoxylates, nonylphenol, and octylphenol by HPLC
(Waters 2695 Separations Module, Waters Ltd.) and Fluorescence Detector (Waters 2475
Multi λ Fluorescence Detector, Waters Ltd.). In this study, the values of risk quotient (RQ) of
APEOs on aquatic organisms were calculated by using following equation: RQ =
MEC/PNEC, where MEC = measured environmental concentrations of APEOs, and PNEC =
predicted no effect concentrations of APEOs on aquatic organisms, which was developed by
USEPA. RQ<1 can be regarded as accepted risk, while RQ >1 represents unaccepted risk.
RESULTS AND DISCUSSION
The analytical results of water quality in samples taken from 18 sampling sites located in
Daniaopi, Hsinhai Bridge I and Hsinhai Bridge II Constructed Wetlands, separately showed
that the percentages of positive testing result for renonylphenol diethoxylates, nonylphenol
monoethoxylates, nonylphenol, and octylphenol were measured equal to 92%, 85%, 17%,
and 74%, respectively with concentrations ranged from <3.3 to 11192.5, <3.3 to 6069.0, <1.3
to 671.0, and <1.0 to 5581.9 ng/L, respectively. However, the average removal efficiencies
from these three different constructed wetlands for renonylphenol diethoxylates, nonylphenol
monoethoxylates, nonylphenol, and octylphenol were measured equal to 58%, 70%, 43%,
and 55%, respectively. Thus, it was concluded that constructed wetland systems performed
ABSTRACTS - WETPOL 2013 - October 13-17, 2013 - Nantes - FRANCE
69
well to remove the EDCs of APEOs treating municipal wastewater. Regarding the ecological
assessment, the calculated values of RQ in the constructed wetland systems used in this study
were up to 30 times higher than the compared constructed wetland systems located in
Pingtung County, Taiwan treating salty water type aquacultural wastewater, in which trace
amounts of APEOs under detecting limited values were found.
Fig. 1. Sketch diagrams and sampling sites for Daniaopi, Hsinhai Bridge I and Hsinhai Bridge II
Constructed Wetland systems, located along Dahan River in Taipei, Taiwan.
CONCLUSIONS
It was concluded that the existing concentrations of EDCs of four different types of
APEOs tested in the constructed wetland systems of this study might cause potential
ecological risks to aquatic organisms. Furthermore, the decreasing risk quotient from influent
to effluent indicating the feasibility and capabilities to treat the EDCs of alkylphenolic
compounds by using constructed wetland systems.
REFERENCES Ahel, M., Molnar, E., Ibric, S., and Giger, W. (2000) Estrogenic metabolites of alkylphenol polyethoxylates in
secondary sewage effluents and rivers. Water Science and Technology, 42, pp. 15-22.
Juang, D.F. and Chen, P.C. (2007) Treatment of polluted river water by a new constructed wetland,
Environmental Science and Technology. 4, pp. 481-488.
ABSTRACTS - WETPOL 2013 - October 13-17, 2013 - Nantes - FRANCE
70
Performance of a cascade constructed wetland treating surfactant
polluted water (O.9)
Jessica Tamiazzo, Simone Breschigliaro, Michela Salvato, Maurizio Borin
DAFNAE – Department of Agronomy, Food, Natural resources, Animals and Environment –
University of Padova, Agripolis Campus, Viale dell’Università 16 – 35020 Legnaro (PD),
Italy ([email protected])
INTRODUCTION
Anionic surfactants are largely used in cleaning sectors, especially in car wash activities
and they are potentially dangerous for the environment, especially for aquatic ecosystem
(Wagener and Schink, 1987).
Urban or industrial treatment systems are able to remove sufficiently the concentration of
anionic and non-ionic surfactants (Gomez et al., 2011). Nevertheless they are expensive, and
constructed wetlands might offer an economic solution (e.g. Mantovi et al., 2003).
In this paper the treatment of anionic surfactants by a pilot constructed wetland designed
to reduce the surface area requirement is presented.
METHODS
The experiment aimed to analyse the performance of an innovative pilot constructed
wetland system (CW), arranged in “cascade”, made of three tanks in series placed at different
elevations: the first tank receives the wastewater from the wastewater reservoir and
discharges by gravity to the second tank that is connected with a third tank and finally to the
outlet. In this way the treatment cells may be installed in vertical, on the side of buildings,
saving significant surface area.
The experiment was conducted in a plant nursery near Padua, Italy. The “cascade” CW
was made of six lines of three tanks each, filled with leca (light expanded clay aggregate),
0.50x0.40x0.29 m in length, width and height respectively, with a tap to discharge the water
(Figure 1). The lines were vegetated with Typhoides arundinacea L. (Moench), Mentha
aquatica L. and Carex divisa Hudson with two replications per species.
Fig. 1. On the left: experimental plant scheme; on the right: transit system of the wastewater in the tank.
To simulate the car washes wastes a synthetic wastewater was created, mixing tap water
and a common carwash cleaning detergent (Autoflash, Kimicar®) to achieve anionic
surfactants concentrations of 10, 50 and 100 mg L-1
that were used in different loading cycles
carried out in October and November 2010 and May-August 2011.
ABSTRACTS - WETPOL 2013 - October 13-17, 2013 - Nantes - FRANCE
71
Concentrations at outlet were analysed and discharge measured every seven days, as
residence time of CWS. In the final phase, with input concentration of 100 mg L-1
, samples at
outlet were also analysed giving only three days of residence time, increasing the flow rate.
The surfactant analysis was conducted using a Hach-Lange spectrophotometer, DR 2800.
RESULTS AND DISCUSSION
The concentrations measured at the outlet were decisively lower respect to the inlet at all
the inlet concentrations. No statistic differences were obtained among plants that were not
damaged by the surfactant, even at the highest concentration. The highest abatement (98,8%)
was obtained with inlet concentration of 100 mg L-1
and reduced residence time.
The amount of anionic surfactants removed increased increasing the inlet concentration.
With input concentrations of 100 mg L-1
the removal was 17 and 34 g m-2
with 7 and 3 days
of HRT respectively (Figure 2).
0
1
2
3
4
5
6
7
10 50 100 100 AP
Ou
tlet co
ncen
trati
on
(m
g L
-1)
Inlet concentration (mg L-1)
0
5
10
15
20
25
30
35
40
45
10 50 100 100 AP
Rem
ov
al
qu
an
tity
(g
m-2
)
Inlet concentration (mg L-1)
Fig. 2. Anionic surfactants concentrations (mg L-1
) and removal (g m-2
) at outlet in relation to inlet.
CONCLUSIONS
The pilot “cascade” system well performed in abating surfactants pollution even at very
high concentrations and represents an interesting perspective to implement wetland treatment
where limited surface is available. The studied plants had similar efficiency and were not
damaged by the high concentrations of surfactant applied.
ACKNOWLEDGEMENTS
Research carried out with the financial support of MIPAF OIGA 2009 Project
“Reproduction, cultivation and evaluation of vegetal species for environmental purposes”.
REFERENCES Gomez, V., Ferreres, L., and Pocurull, F. (2011) Determination of non-ionic and anionic surfactants in
environmental water matrices. Talanta 84:859-866.
Mantovi, P., Marmiroli, M., Maestri, E., Tagliavini, S., Piccinini, S., and Marmiroli, N.(2003) Application of a
horizontal subsurface flow constructed wetland on treatment of dairy parlor wastewater. Bioresource
Technology 88: 85–94.
Wagener, S., and Schink, B. (1987) Anaerobic degradation of nonionic and anionic surfactants in
enrichment cultures and fixed-bed reactors. Water Research 21(5):615–622.
ABSTRACTS - WETPOL 2013 - October 13-17, 2013 - Nantes - FRANCE
72
Perchloroethene removal in a plant root mat filter and horizontal
subsurface flow constructed wetland treating a sulfate rich
contaminated groundwater (O.21)
Zhongbing Chen, Peter Kuschk
Department of Environmental Biotechnology, Helmholtz Centre for Environmental Research
– UFZ, Permoserstrasse 15, 04318 Leipzig, Germany ([email protected])
INTRODUCTION
Because of improper uses and storage, PCE has been recognized as being among the most
ubiquitous groundwater contaminants. PCE and its’ metabolites trichloroethene (TCE),
dichloroethenes (DCEs) and vinyl chloride (VC), are known to be toxic to humans. VC is
even known as a human carcinogen, and is an USEPA priority pollutant with a maximum
contaminant level (MCL) of 2 µg L-1 in drinking water. Anaerobic conditions are necessary
for the first step of reductive dechlorination of PCE to TCE, which can be followed by
reductive dechlorination or oxidation of TCE, dichloroethenes (1,1-DCE, 1,2-trans-DCE, 1,2-
cis-DCE), VC and ethene under anaerobic and/or aerobic conditions (Bradley, 2003; Mattes
et al., 2010). However, the use of CWs for treating chlorinated hydrocarbons contaminated
groundwater is scarce to date (Braeckevelt et al., 2011; Pardue et al., 1999; Kadlec et al.,
2012).
Floating plant root mat is a variant of CWs, in which the plants are no longer rooted in a
soil but grow on floating rafts, or floating by the self-buoyancy of their dense interwoven
roots and rhizomes that form a mat (Headley & Tanner, 2011; Van de Moortel et al., 2010).
When the water level is lowered to such an extent that the mat touches the root proof bottom
of the pond or channel, and the hydraulic flow is forced directly through the root mat, this
system functions as a plant root mat filter (PRMF). The floating plant root mats and the non-
floating PRMFs are not yet broadly applied technologies (Chen et al., 2012; Tanner &
Headley, 2011; Van de Moortel et al., 2010). Especially, no information on the treatment of
water contaminated with chlorinated ethenes by PRMFs is available.
The objective of this study was to compare the treatment of sulfate rich groundwater
contaminated with PCE in two pilot-scale CWs (a horizontal subsurface flow (HSSF)-CW
and a PRMF).
METHODS
The HSSF CW was established in March 2003 and the PRMF in March 2010 in Bitterfeld,
Germany. Each system consisted of a container with 6 m length, 1 m width and 0.6 m height.
The HSSF CW was filled with the local aquifer material to a height of 0.5 m and planted with
common reed (Phragmites australis). More details about this HSSF CW are described
elsewhere (Braeckevelt et al., 2011). The PRMF was set with 3 years old well developed
plant root mats of a height of about 30 cm of common reed with densely interwoven roots.
Both systems were continuously supplied with contaminated groundwater with a flow rate of
5.0 L/h. The inflow concentration of PCE is about 2 mg L-1 and sulfate concentration is
around 850 mg L-1.
RESULTS AND DISCUSSION
PCE was removed completely after a flow path of 4 m during the recorded period in the
HSSF CW. However, in the PRMF a similar PCE removal performance was only reached
during summer period. This could be due to the temperature effect on the microbial activity,
ABSTRACTS - WETPOL 2013 - October 13-17, 2013 - Nantes - FRANCE
73
as the soil free PRMF seems to be more sensitive than the soil based HSSF CW; so, in the
PRMF the temperature was during summer about 1°C higher and during winter about 1 °C
lower than in the HSSF CW). On the other hand, the plant activity was stable during the
summer period (represented by water loss); it can be assumed that during this period plants
release more organic carbon than during the colder seasons which is needed for the anaerobic
dechlorination process. Significant differences of the PCE load along the flow path was found
between the HSSF CW and the PRMF ( P=0.002), which means lower residual PCE load was
found in the HSSF CW in comparison to the PRMF. The HSSF CW showed robust PCE
removal capacity, as all PCE was removed after 0.5 m from the inlet in the HSSF CW. The
difference of PCE concentration in three depths in the HSSF CW was only found at 0.5 m
between the 30 cm with 50 cm and 40 cm with 50 cm (P=0.009 and 0.041, respectively).
CONCLUSIONS
The PRMF showed lower removal efficiency for PCE than the HSSF CW. Nevertheless,
during the summer period PCE was also completely removed like in the HSSF CW. In
comparison to the HSSF CW, not all dechlorination products could be detected, especially
VC and ethene, which are preferably metabolized by microorganisms via an aerobic pathway.
The PRMF seems to be more suitable for the removal of contaminants which need oxic
condition like low chlorinated hydrocarbons as VC for their microbial degradation, while
HSSF CW provide better conditions for microbial anaerobic processes like the dechlorination
of highly chlorinated hydrocarbons as PCE prevail.
REFERENCES Bradley, P.M. 2003. History and Ecology of Chloroethene Biodegradation: A Review. Bioremediat. J., 7(2), 81-
109.
Braeckevelt, M., Seeger, E.M., Paschke, H., Kuschk, P., Kaestner, M. (2011). Adaptation of a Constructed
Wetland to Simultaneous Treatment of Monochlorobenzene and Perchloroethene. Int. J. Phytoremediation.,
13(10), 998-1013.
Chen, Z., Kuschk, P., Reiche, N., Borsdorf, H., Kästner, M., Köser, H. 2012. Comparative evaluation of pilot
scale horizontal subsurface-flow constructed wetlands and plant root mats for treating groundwater
contaminated with benzene and MTBE. J. Hazard. Mater., 209–210, 510-515.
Headley, T.R., Tanner, C.C. 2011. Constructed Wetlands with Floating Emergent Macrophytes: an innovative
stormwater treatment technology. Crit. Rev. Environ. Sci. Technol., In press.
Kadlec, R.H., Martin, D.C., Tsao, D. 2012. Constructed marshes for control of chlorinated ethenes: An 11-year
study. Ecol.Eng., 46(0), 11-23.
Mattes, T.E., Alexander, A.K., Coleman, N.V. 2010. Aerobic biodegradation of the chloroethenes: pathways,
enzymes, ecology, and evolution. FEMS Microbiology Reviews, 34(4), 445-475.
Pardue, J.H., Kassenga, G., Shin, W.S. 1999. Design approaches for chlorinated VOC treatment wetland.
Wetlands and Remediation: An International Conference, Salt Lake City, Utah. Batelle Press, Columbus(OH),
USA. pp. 301–308.
Tanner, C.C., Headley, T.R. 2011. Components of floating emergent macrophyte treatment wetlands influencing
removal of stormwater pollutants. Eco. Eng., 37(3), 474-486.
Van de Moortel, A., Meers, E., De Pauw, N., Tack, F. 2010. Effects of Vegetation, Season and Temperature on
the Removal of Pollutants in Experimental Floating Treatment Wetlands. Water Air Soil Pollut., 212(1), 281-
297.
ABSTRACTS - WETPOL 2013 - October 13-17, 2013 - Nantes - FRANCE
74
Transport and biodegradation of chloroacetanilide herbicides in
lab-scale wetlands (O.23)
G. Imfelda, E. Maillard
a, O.F. Elsayed
a, I. Nijenhuis
b, M. Millet
c
a Laboratory of Surface Hydrology and Geochemistry of Strasbourg (LHyGeS), UMR7517
University of Strasbourg - CNRS, France
b Department of Isotope Biogeochemistry, Helmholtz Centre for Environmental Research
(UFZ), Leipzig, Germany
c Atmospheric Physical Chemistry Department (LMSPC), University of Strasbourg, UMR
7515 CNRS, France
INTRODUCTION
Chloroacetanilide herbicides, such as metolachlor, alachlor and acetochlor, are used for
control of annual grasses and broad-leaved weeds on a variety of crops including maize,
sugar beet and sunflower. The extensive use of chloroacetanilide herbicides is reflected in
their frequent detection in ground and surface waters. Wetland systems can intercept upward
flow of pesticide-contaminated water from shallow aquifers during groundwater discharge.
Knowledge on the transfer and biodegradation of chloroacetanilide herbicide in wetlands in
relation with biogeochemical conditions is very scarce. Compound-specific stable isotope
analysis (CSIA) is a promising approach for the assessment of contaminant degradation in the
environment, but has not yet been reported for the evaluation of pesticide biodegradation in
wetlands.
Here, we examined the transfer and biodegradation of metolachlor, alachlor and acetochlor
in lab-scale wetlands using a comprehensive approach that combine hydrochemical, chiral
and compound-specific isotope analyses. The lab-scale wetlands were designed to investigate
the influence of upward discharge of pesticide-contaminated groundwater into wetland
systems.
METHODS
The experimental design consisted of 4 wetland columns (diameter: 15 cm, height: 65 cm).
3 columns were separately and continuously supplied with 1.8 µM (~500 µg L-1
, i.e. runoff
concentration after herbicide application) of Rac-metolachlor, acetochlor and alachlor spiked
in fresh runoff water from a vegetated ditch collecting runoff-associated chloroacetanilides
from agricultural land (background herbicide concentration < 2 µg L-1
). A fourth column
(control) was supplied with runoff water only. The wetlands were filled with gravel and sand
and planted with Phragmites australis (Cav.), kept at 20 °C ± 0.5 °C, and exposed to LED
lamp light for 8 h d-1
. The nominal residence time was 9.3 days (bromide tracer experiment).
The experiment was carried out over 202 days. The continuous injection of
chloroacetanilides in the wetlands was preceded by an inoculation period of 104 days during
which runoff water was supplied without herbicides. Porewater samples were collected at the
inlet and outlet of each column, and from sampling ports mounted at 15, 25, 35, 45 and 55 cm
from the inlet point. The sampling campaigns were carried out biweekly at 0, 14, 28, 42, 56,
70, 84 and 98 days after the chloroacetanilide injection started.
Dissolved organic carbon, major and trace ions, total phosphorous, total sulfur and metals
were quantified by FR EN ISO standards and laboratory procedures. Chloroacetanilide
herbicides in water samples were extracted using a solid-phase extraction (SPE) procedure
and quantified with a GC-MS equipped with a chiral column. The carbon isotope
ABSTRACTS - WETPOL 2013 - October 13-17, 2013 - Nantes - FRANCE
75
composition of chloroacetanilides was analysed using a GC-C-IRMS system consisting of a
gas chromatograph coupled via a GC/C III interface to an isotope ratio mass spectrometer.
RESULTS AND DISCUSSION
A spatial gradient of oxygen concentrations was observed in the four lab-scale wetlands
with oxic conditions (212 ± 24 µM) prevailing at the bottom of the wetlands between 15-25
cm, and anoxic conditions between 45-55 cm from inlet points. Nitrate depletion observed in
the four wetlands suggests the occurrence of nitrate reducing conditions in anoxic zones
towards wetlands outlets. The high removal between day 0 and 28 was mainly attributed to
sorption. Removal of acetochlor and alachlor loads from inlets to outlets from day 28 to day
98 averaged 56 ± 6% and 53 ± 11%, respectively, whereas metolachlor was more persistent
(average mass removal of 23 ± 5%) (Fig. 1). A bulkier alkoxyethyl side chain leading to
greater steric hindrance around the carbon chlorine bond and lower degradation rates may
explain the greater persistence of metolachlor.
Fig. 1. Temporal change of metolachlor, alachlor and acetochlor mass removal in the wetlands.
Biodegradation occurred mainly in anoxic zones as evidenced by both concentration
analysis and CSIA. Enrichment factors could not be calculated for metolachlor because
changes in the isotopic composition were ≤ 0.8‰. Carbon isotope fractionation indicated in
situ biodegradation of alachlor (Ɛbulk = -2.0 ± 0.3) and acetochlor (Ɛbulk = -3.4 ± 0.5). Similar
enrichment factors over time suggest that the same degradation pathways prevailed in the
wetland throughout the investigation period. An orbitrap-based MS analysis revealed the
occurrence of 3 to 4 degradation products in each wetland. The enantiomeric separation of
metolachlor revealed EF(S) < 0.5, which suggests enantioselective degradation at the outlet.
CONCLUSIONS
Based on a multiple-method approach, the results underscore the linkage between the
changes of hydrochemical conditions and degradation of chloroacetanilide herbicides in
wetland systems. Our results indicate moderate mass removal for acetochlor and alachlor and
lower removal for metolachlor in wetland systems. Enantioselective degradations could affect
the fate of metolachlor in wetland environments, and emphasise the role of chirality in
pesticide degradation. This study is also a first step towards the application of CSIA to
evaluate the fate of chloroacetanilide herbicides in wetlands and other complex environments.
ACKNOWLEDGEMENTS
This research has been funded by the European Union under the 7th Framework
Programme (Marie Curie ITN CSI:ENVIRONMENT, contract number PITN-GA-2010-
264329.) and the PhytoRET project (C.21) of the European INTERREG IV program Upper
Rhine.
ABSTRACTS - WETPOL 2013 - October 13-17, 2013 - Nantes - FRANCE
76
Response of a free-water surface constructed wetland after a
Cr(VI) accidental dump (O.39)
Maine, M.A.1,2
, Sánchez, G.C.1, Mufarrege M.M.
2, Hadad, H.R.
2, Di Luca,
G.A.2, Caffaratti, S.E.
1, Pedro, M.C.
1
1Química Analítica, Facultad de Ingeniería Química, Universidad Nacional del Litoral.
Santiago del Estero 2829 (3000) Santa Fe, Argentina ([email protected]) 2Consejo Nacional de Investigaciones Científicas y Técnicas (CONICET), Argentina.
INTRODUCTION Constructed wetlands (CW) are often designed as secondary or tertiary treatments for
industrial wastewater (Kadlec and Wallace, 2009). CWs efficiently decrease mean
concentrations and variability concentrations of contaminants in water. This regulation
capacity implies an important advantage: if the primary treatment failed and there was an
accidental load of high concentrations of contaminants, the CW would retain them. A free-
water surface wetland was constructed and planted with Typha domingensis (cattail) at a
metallurgic industry. The effluent to be treated is composed of industrial wastewater and
sewage (both had previously received a primary treatment). The primary treatment of the
industrial effluent consists of the reduction of Cr(VI) to Cr (III) and the subsequent
oxihydroxides precipitation. This wetland normally receives effluents with Cr concentrations
of 0.10-3.5 mg l-1
. The aim of this work was to evaluate the response of the wetland system
faced with an accidental dump of Cr(VI).
METHODS
A metallurgical effluent with a concentration of 200 mg l-1
Cr(VI) was poured in the
wetland for 8 hs. Then, the wetland was closed for 30 days, avoiding the effluent outflow.
Cr(VI), total Cr, pH and conductivity were measured in the effluent in the inlet and outlet
area. Cr was also determined in T. domingensis (root and leaf), sediment and plant detritus at
the beginning and 30 days after the dumping. Cr(VI) concentration was determined
colorimetrically. Total Cr concentration was determined in water, sediment and macrophytes
after acid digestion by atomic absorption spectrophotometry.
RESULTS AND DISCUSSION
The concentration of Cr(VI) and total Cr in water decreased significantly in the outlet
effluent (Fig. 1). No significant differences were found between the concentration of total Cr
and Cr(VI) in water over time. Cr(VI) can be reduced by organic matter, Fe(II), dissolved
sulfides, and humic compounds with sulfhidryl groups (Kadlec et al., 2000). In this case,
organic matter probably caused the reduction of Cr(VI) to Cr(III), which immediately
precipitated as oxihydroxides. After the dump, Cr concentration in sediment was significantly
greater in the inlet than in the outlet area, indicating retention by sediment (Table 1). T.
domingensis tolerated the treatment in the outlet area while it died in the inlet area. A layer of
plant detritus covered the sediment in the inlet area. Plant detritus showed higher Cr
concentration than sediments (Table 2). Cr concentration increased significantly in root
tissues of the inlet area, reaching values higher than those reported in literature (Dotro et al.,
2009; Maine et al., 2007). Cr concentration in leaves was significantly lower than that found
in roots, indicating low translocation. As Cr concentration in water decreased after 30 days,
the wetland was emptied, plant detritus containing high Cr concentrations was removed and
new specimens of T. domingensis were planted in the inlet area.
ABSTRACTS - WETPOL 2013 - October 13-17, 2013 - Nantes - FRANCE
77
Fig 1. Cr(VI) and total Cr concentrations (mg l-1 ) in water at the wetland outlet
Table 1. Total Cr concentrations (mg g
-1) in sediment at the wetland inlet and outlet
Sediment Inlet Outlet
Initial 0.065 0.016
After 30 days 0.916 0.070
Table 2. Total Cr concentrations (mg g
-1) at the wetland inlet and outlet
Inlet Outlet
Initial conditions Leaf Root Leaf Root
T. domingensis 0.024 0.535 0.011 0.068
After 30 days
T. domingensis 0.677 12.44 0.042 0.715
Plant detritus 11.62 1.98
CONCLUSIONS
Cr(VI) was efficiently removed from water after 30 days. Accumulation of Cr in
sediment, plant detritus and root plants were the pathways responsible for the
disappearance of Cr from water.
Plant detritus with high Cr concentration was easily removed from the wetland.
T. domingensis accumulated high Cr concentrations and was affected in the inlet
area while it did not show phytotoxic symptoms in the outlet area.
90 days after the dump, the wetland restarted its normal operation, demonstrating
the robustness of this treatment system.
ACKNOWLEDGEMENTS
The authors thank Consejo Nacional de Investigaciones Científicas y Técnicas
(CONICET), Universidad Nacional del Litoral (UNL)-CAI+D Project and Agencia de
Promoción Científica y Tecnológica for providing funds for this work.
REFERENCES Dotro G., Palazolo P. and Larsen D. (2009) Chromium fate in constructed wetlands treating tannery
wastewaters. Wat. Environ. Res., 81(6):617-625.
Kadlec, R.H., Knight, R.L., Vymazal, J., Brix, H., Cooper, P. and Haberl, R. (2000) Constructed Wetlands for
Pollution Control: Processes, Performance, Design and Operation. IWA Publishing.
Kadlec, R.H. and Wallace, S.D. (2009) Treatment Wetlands, CRC Press, Boca Raton, Florida. 893p.
Maine, M.A., Suñé, N., Hadad, H.R., Sánchez, G. and Bonetto, C. (2007) Removal effciency of a constructed
wetland for wastewater treatment according to vegetation dominance. Chemosphere. 68:1105-1113.
0
20
40
60
80
100
120
140
0 2 4 6 8 10 12 14 16 18 20 22 24 26 28 30
Days
mg
l-1 C
r
Total Cr Cr(VI)
ABSTRACTS - WETPOL 2013 - October 13-17, 2013 - Nantes - FRANCE
78
Use of rewetted fen peatlands for the degradation of emerging
pollutants (O.43)
Sebastian Maassen, Dagmar Balla, Ralf Dannowski
Leibniz Centre for Agricultural Landscape Research (ZALF), Institute of Landscape
Hydrology, Eberswalder Strasse 84, Müncheberg, 15374, GERMANY ([email protected],
[email protected], [email protected])
INTRODUCTION
In a joint research project (ELaN) started in 2011, we are analyzing degraded fen soils of
the Randow-Welse lowlands in the sparsely populated rural Uckermark region in
northeastern Germany with reference to their suitability for biomass production (short
rotation coppice, reeds). In terms of sustainability, peat mineralization processes have to be
reduced by high water levels. Because of the negative water budget during the vegetation
period, supplemental water pumped from the channel system is required to be given upon the
surface for rewetting (Dannowski & Balla 2004). Rewetted fen peatlands could be integrated
into water protection purposes by the additional purification of treated waste water. We
hypothesize that with the application of treated waste water on rewetted peat sites the
potential for the anaerobic decay of emerging pollutants increases due to both, high organic
matter/DOC content in the peat as well as a prolonged residence time during the groundwater
passage as shown in Fig. 1.
Fig. 1. Schematic of the use of rewetted fen sites for energy plant production and as an additional cleaning
stage for waste water treatment.
The feasibility of this idea strongly depends on the proof of harmlessness for the
groundwater quality. In order to protect groundwater bodies from hazardous substances, all
regulations allow the utilization of treated waste water only in limited boundaries. Hence, our
investigations are focused on the proof of the environmental compatibility with respect to
groundwater protection. The study site had previously been rewetted with supplemental water
in an earlier research campaign from 1996 to 2002. From 2002 to 2011, the site was
abandoned and intensified peat mineralization took place. Our intention is also to deal with
the site’s abiotic aspects after intermediately losing the rewetting status.
METHODS
The Biesenbrow site (8 ha) located in the Randow-Welse valley (Uckermark, state of
Brandenburg) consists of fen peat up to 120 cm in thickness which in former time was
drained and sub-irrigated under intensive grassland use. During the rewetting period 1996-
2002, an abiotic monitoring of soil parameters as well as ground- and surface water chemistry
was performed (Balla et al., 2004). Before the re-start of rewetting in 2011, a topographical
survey and groundwater chemistry analysis were performed at the site. Groundwater
monitoring wells in three depths (2, 4, 6 m) were installed to screen the groundwater quality
(a) common practice for the discharge
of treated waste water (as quickly as
possible into the running water system)
(b) hypothesized bypass flux using the
anaerobic peat layer and long travel
times (t > months or years) passing the
groundwater body into the receiving
surface waters
ABSTRACTS - WETPOL 2013 - October 13-17, 2013 - Nantes - FRANCE
79
with regard to emerging pollutants, heavy metals, cations and anions. The residence time in
groundwater will be modeled by the finite element Model FEFLOW (DHI-WASY). To
calibrate the model, thermodynamic parameters at the channel bottom are measured and the
water and mass flux from the rewetted site into the surrounding channels is determined
(Maassen and Balla, 2010).
RESULTS AND DISCUSSION
In comparison of the original geodetic survey before rewetting in 1995, in 2011 the area
has lost 6.6 cm in height in average of all measurement points, with minimum of 0 and
maximum of 18 cm. The elevation differences are heterogeneously distributed. Related to the
16 years without cultivation (no plowing, no fertilizer, no biomass removal), the loss in
elevation is approximately 0.4 cm per year. The water chemistry of the monitored
groundwater wells showed a significant increase of the sulfate concentration (SO4), as well as
a decrease of soluble phosphorus (SRP) and dissolved organic carbon (DOC). The chloride
concentration (Cl) was nearly constant. The obvious rise of sulfate is most likely attributed to
peat mineralization and the release of soil bound sulfur, whereas the trends of the other
parameters might be a result of regional mineralized groundwater upwelling through the peat
layer beyond the irrigation period. After nearly two years of irrigation with addition of treated
wastewater (6 months during the growing seasons of 2011 and 2012), approximately
4,000 m3 of treated wastewater mixed with 30,000 m
3 of channel water was applied at an area
of 4 ha. There were no adverse effects on groundwater quality detectable. Some groups of
substances show "hot spots" in the concentrations in treated wastewater (e.g. pharmaceuticals
Diclofenac and Carbamazepine, flame retardant tris-(chlorisopropyl)-phosphate).
CONCLUSIONS
In degraded fens rewetted with admixture of treated wastewater, added value can be
achieved by biomass production and an extra purification of the wastewater, particularly in
rural areas without the intention of the immediate use of the groundwater resource. Therefore,
the inclusion of degraded fens into future infrastructures for the disposal and usage of
wastewater could be a promising alternative for the conservation of surface water systems.
ACKNOWLEDGEMENTS
The ELaN project (www.elan-bb.de) is funded by the Federal Ministry of Education and
Research within the funding activity "Sustainable Land Management".
REFERENCES Balla, D., Velty, S. and Dannowski R. (2004) Wirkung einer Wiedervernässungsmaßnahme auf das Grund- und
Oberflächenwasser – Pilotanlage Biesenbrow. Archiv für Naturschutz und Landschaftsforschung 43:41-58.
Dannowski, R. and Balla, D. (2004) Wasserhaushalt und geohydrologische Situation einer vernässten
Niedermoorfläche mit Schilfanbau in Nordost-Brandenburg. Archiv für Naturschutz und Landschaftsforschung
43:27-40.
Maassen, S. and Balla, D. (2010) Impact of hydrodynamics (ex- and infiltration) on the microbially controlled
phosphorus mobility in running water sediments of a cultivated northeast German wetland. Ecol. Eng. 36
(9):1146-1155.
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80
Pesticide transport, partitioning and distribution in a stormwater
wetland collecting runoff from a vineyard catchment (O.53)
E. Maillarda and G. Imfeld
a
aLaboratory of Hydrology and Geochemistry of Strasbourg (LHyGeS), University of Strasbourg/ENGEES,
CNRS, 1 rue Blessig, 67084 Strasbourg Cedex, FRANCE ([email protected]; [email protected])
INTRODUCTION
Wetlands are biogeochemically active zones that may intercept pesticide-contaminated
runoff and contribute to pesticide attenuation before they reach aquatic ecosystems (Imfeld et
al, 2009). The transport and fate of pesticides in wetlands is mainly governed by their
partitioning between the solid and aqueous phases, and their distribution between the
different compartments (i.e. bed sediments, vegetation, water and organisms). Although
several studies have focused on pesticides in wetlands (Maillard et al, 2012), the distribution
of runoff-associated pesticides between wetland compartments has never been quantified.
There is a need to identify the major pools of pesticides in wetland systems and quantify their
change over time to better understand wetland functioning with respect to pesticide
metabolism. In this study, we used a mass-balance approach to quantify, throughout an entire
season, runoff-associated herbicides and fungicides and their distribution among the different
compartments of a stormwater wetland collecting pesticide runoff.
MATERIAL AND METHODS
The studied stormwater wetland (Rouffach, France) is located at the outlet of a 42 ha
vineyard catchment. The wetland has a surface area of 319 m2 (including a forebay and a
gravel filter), a residence time of about 10 h, and is naturally planted with common reeds. 11
fungicides, 1 herbicide and 1 degradation product were monitored from March to September
2011. Runoff discharges were continuously measured at the inlet and outlet of the wetland
and weekly composite water samples were collected. Pesticides were quantified in suspended
solids (> 0.7 µm), and in < 0.7 µm and < 0.22 µm filtrate water. A mass balance was
established to quantify monthly the pesticide amount in the vegetation and
macroinvertebrates biomasses, as well as in the wetland water and sediments.
RESULTS AND DISCUSSION
During the investigation period, 1944 m3 of runoff water entered the stormwater wetland,
leading to a total input of 33.6 tons of suspended solids (> 0.7 µm).
Fig. 1. Relative loads of pesticides associated with suspended solids (> 0.7 µm) and in the
aqueous phase (< 0.7 µm) at the inlet (A) and the outlet (B) of the studied stormwater wetland.
Rat
io L
oad
/ L
oad
to
t [%
] Ratio Load /
Load tot
[%]
ABSTRACTS - WETPOL 2013 - October 13-17, 2013 - Nantes - FRANCE
81
In the same time, 58.8 g of dissolved pesticides and 3.0 g of particle-laden pesticides
entered the wetland over the season. Outlet pesticide loads were 2.3 g and 56.6 mg,
respectively in the dissolved and in the particulate phase. Pesticide partitioning differed
according to molecule properties (Fig.1). The removal efficiency varied over time with
respect to hydrological and biogeochemical conditions in the wetland, and was 96.1% for
dissolved pesticides and 98.1% for particle-associated pesticides.
Glyphosate, AMPA and dithiocarbamates were molecules with the largest loadings in the
wetland (Fig.2). The highest pesticide loads (26.3 g) were detected in the wetland fine bed
sediments (< 250 um) and in the SS (13.3 g) trapped by the gravel filter, especially at the end
of the season, in September. This highlights the large pesticide trapping efficiency of wetland
sediments and wetland-intrinsic biotransformation processes. In contrast, coarser sediments
(> 1mm), wetland vegetation and macroinvertebrates biomasses bore less pesticide amounts.
Pesticide loads bound to the vegetation, and in particular to the roots, decreased over time,
suggesting that the root zone was mainly involved in pesticide transformation/degradation.
CONCLUSIONS
This study shows that wetlands are efficient for trapping both dissolved and sorbed
pesticides. This is the first time that a detailed quantification of pesticide pools within a
wetland is provided. This enabled to identify which compartments mainly contribute to
pesticide transport, accumulation (i.e. bed sediments) or transformation (i.e. roots
compartment). Pesticide accumulation in sediments raises the issue of pesticide
remobilization and their management after dredging operations. We anticipate our results to
be a starting point for the quantitative analysis of pesticide partitioning among wetland
compartments, with further implications for the ecotoxicological risks associated with
pesticide runoff.
ACKNOWLEDGEMENTS This research has been funded by the PhytoRET project (C.21) of the European INTERREG IV program
Upper Rhine. Elodie Maillard was supported by a fellowship of U.E. and the Alsace region.
REFERENCES Imfeld G, Braeckevelt M, Kuschk P and Richnow HH (2009) Monitoring and assessing processes of organic
chemicals removal in constructed wetlands. Chemosphere 74, pp. 349-362
Maillard E, Payraudeau S, Ortiz F and Imfeld G, (2012) Removal of dissolved pesticide mixtures by a
stormwater wetland receiving runoff from a vineyard catchment: an inter annual comparison. International
Journal of Environmental Analytical Chemistry, Volume 92, Issue 8, pp. 979-994.
Fig. 2. Distribution of the pesticide mixture between the different compartments of the wetland.
Ratio Load /
Load tot
[%]
Wetland compartments
203 Total loads [mg] 461 505 26258 121
909 33 0.5 200 13388 1920
2092 75
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82
Removal of emerging organic contaminants in hybrid constructed
wetlands for the treatment of wastewater of small communities of
warm climate regions (O.54)
Cristina Ávilaa, Carlos Aragón
b, Isabel Martín
b, Juan J. Salas
b, Josep M.
Bayonac, Joan García
a
aGEMMA-Group of Environmental Engineering and Microbiology, Department of
Hydraulic, Maritime and Environmental Engineering, Universitat Politècnica de Catalunya-
BarcelonaTech, c/Jordi Girona, 1-3, Building D1, Barcelona, 08034, SPAIN
([email protected], [email protected])
bFoundation Centre for New Water Technologies (CENTA). Autovía Sevilla-Huelva (A-49),
km. 28. Carrión de los Céspedes, Seville, 41820, SPAIN ([email protected],
[email protected], [email protected])
cDepartment of Environmental Chemistry, IDAEA-CSIC, c/Jordi Girona, 18-26, Barcelona,
08034, SPAIN ([email protected])
INTRODUCTION
Constructed wetlands (CWs) constitute a good alternative for wastewater treatment of
small communities worldwide. A comprehensive approach aiming at combining different
types of CWs proved to be a highly efficient ecotechnology for an integrated sanitation of
small communities in warm climates, holding very low O&M requirements (Ávila et al.,
2013). It produced a good final effluent for its reuse after the treatment of combined sewer
effluent, even at stormy periods and first-flush events. However, the occurrence of emerging
organic contaminants (EOCs) in poorly treated wastewater and eventually in other
watercourses constitutes nowadays an increasing concern worldwide due to their possible
toxicological effects to the environment and living organisms. The application of reclaimed
water could pose unknown undesirable effects to the environment and thus the occurrence
and behavior of EOCs in this type of treatment systems should be further studied.
The scope of this study was to evaluate the efficiency of a full-scale hybrid CW system
located in Seville (southern Spain) on the removal of several EOCs (i.e. ibuprofen –IB-,
diclofenac –DCF-, acetaminophen –ACE-, carbamazepine –CBZ-, ethinyl estradiol –EE2-,
tonalide –AHTN-, oxybenzone –OXY-, triclosan –TCS-, bisphenol A –BPA-) from a
combined sewer effluent.
METHODS
The hybrid treatment system was part of a larger pilot-scale treatment plant that received
the wastewater from 2500 P.E. from the municipality of Carrión de los Céspedes (Seville,
Spain) together with the runoff collected in a combined sewer system. The treatment line
consisted of an imhoff tank followed by a 317 m2 vertical subsurface flow CW (VF), a 229
m2 horizontal subsurface flow CW (HF) and a 240 m
2 free water surface CW (FWS) in
series. They were all planted with Phragmites australis and received an average flow of 14
m3 d
-1. The VF received an average organic loading rate of about 9 g BOD5 m
-2 d
-1 and an
average hydraulic loading rate of 44 mm d-1
. The final effluent was collected in a 20 m3 open-
air water tank working as a raft for irrigation.
Effluent 24-h composite samples of the different treatment units were grabbed once a
week (n = 8) from May to June 2011. They were transported to the laboratory in 250 mL
amber glass bottles and kept refrigerated at 4ºC until analysis (sample holding time < 1 day).
Samples were analysed for EOCs as described elsewhere (Matamoros and Bayona, 2006).
ABSTRACTS - WETPOL 2013 - October 13-17, 2013 - Nantes - FRANCE
83
RESULTS AND DISCUSSION
Mean values and standard deviations of wastewater quality parameters along the treatment
line are shown in Table 1. The hybrid CW system was very efficient on their removal.
Results for EOCs (Fig. 1) showed that they could be categorized as (i) efficiently removed
compounds with removal higher than 85% (IB, ACE, AHTN, BPA) and (ii) moderately
removed compounds with removal efficiencies between 50% and 85% (DCF, CBZ, TCS).
EE2 and OXY were <LOD in every sampling point throughout the study. The removal of
ACE took place completely in the VF wetland. Table 1. Wastewater physico-chemical characteristics at the effluent of the different treatment units along
the treatment line. Mean values and standard deviations are shown.
Influent Imhoff tank VF HF FWS
T (°C) 23.8 ± 1.7 24.0 ± 1.7 22.8 ± 1.6 22.2 ± 1.7 19.9 ± 1.7
DO (mg L-1
) 0.2 ± 0.0 0.2 ± 0.0 2.0 ± 1.7 4.2 ± 0.4 2.7 ± 0.3
Eh (mV) -138 ± 8 -198 ± 31 -124 ± 9 -61 ± 44 -71 ± 61
TSS (mg L-1
) 212 ± 59 114 ± 33 9 ± 4 15 ± 5 6 ± 2
BOD5 (mg L-1
) 320 ± 57 125 ± 7 11 ± 8 7 ± 2 6 ± 2
TN (mg L-1
) 40.1 ± 8.8 38.5 ± 6.1 13.3 ± 3.6 3.6 ± 1.4 2.4 ± 0.6
TP (mg L-1
) 5.9 ± 1.2 5.9 ± 1.6 5.3 ± 1.8 4.2 ± 2.0 3.1 ± 0.4
Ibup
rofe
n
Diclofe
nac
Ace
tam
inop
hen
Car
bam
azep
ine
EE2
Tonalide
Oxy
benz
one
Bisph
enol A
Triclosa
n
Co
nce
ntr
atio
n (
g L
-1)
0
1
2
3
4
5
6
14
16
18
20
22 Influent
Imhoff
VF
HF
FWS
Ibup
rofe
n
Diclofe
nac
Car
bam
azep
ine
Tonalide
Bisph
enol A
Triclosa
n
Re
mo
va
l e
ffic
ien
cy (
%)
0
20
40
60
80
100 VF
HF
FWS
Figure 1. (a) Concentration of the different EOCs along the treatment line; (b) Accumulated removal
efficiencies of selected EOCs at the different units of the hybrid CW system.
The experimental system appears as an integrated approach capable of accomplishing a
good removal of EOCs. This reinforces the idea of hybrid CWs as very robust systems for
wastewater treatment and reuse in small communities. Since monitoring was carried out in
summer season, the performance in winter time should be further evaluated.
ACKNOWLEDGEMENTS
This research has been funded by the Spanish Ministry of Environment (MMARM)
through the Project No. 085/RN08/03.2. Ms. Cristina Avila kindly acknowledges a
predoctoral fellowship from the Universitat Politècnica de Catalunya. BarcelonaTech.
REFERENCES Ávila, C., Salas, J.J., Martín, I., Aragón, C. and García, J. (2013) Integrated treatment of combined sewer
wastewater and stormwater in a hybrid constructed wetland in southern Spain and its further reuse. Ecological
Engineering 50:13-20.
Matamoros V. and Bayona J.M. (2006) Elimination of pharmaceuticals and personal care products in subsurface
flow constructed wetlands. Environmental Science and Technology 40:5811-5816.
(a) (b)
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84
Temporal and Spatial Dynamics of Organochlorine Pesticides in
the Suspended Particulate Matter from Lake Chaohu (O.96)
Fu-Liu Xu, Qing-Mei Wang, Wei He, Ning Qin, Xiang-Zhen Kong,
MOE Laboratory for Earth Surface Process, College of Urban & Environmental Sciences,
Peking University, Beijing 100871, China ([email protected])
INTRODUCTION
China is one of the countries with the largest amount production and usage of
organochlorine pesticides (OCPs) in the world. Some OCPs such as DDTs have been banned
to use in China since 1983; however, they are still detected in various environmental and
biological media (Tao et al., 2008). In the present study, the residual level, temporal-spatial
variation, composition, potential sources and ecological risks of OCPs in the SPM from Lake
Chaohu, the fifth largest lake in China were studied.
METHODS
The SPM samples were collected monthly through the filtration of water samples from
four sites located in the eastern, central and western area of Lake Chaohu during May 2010 to
April 2011. The Microwave-assisted extraction method and a silica gel-neutral alumina
mixed column were used to extract and purify the SPM samples. OCPs in the SPM samples
were analysed by GC-MS.
RESULTS AND DISCUSSION
Residues of OCPs in the SPM
Seventeen types of OCPs were detected in the SPM samples. The annual average
concentration of total OCPs in the SPM was 172.68 ± 434.88 ng/g. The residual level of
DDTs was the highest (138.76 ± 407.27 ng/g), accounting for 80.4% of the total OCPs,
followed by HCHs (15.08 ± 10.30 ng/g) and HCB (9.74 ± 15.77 ng/g), accounting for 8.7%
and 5.6% of the total OCPs, respectively.
The temporal-spatial variations of OCPs in the SPM
The spatial distribution of OCPs in the SPM followed such order as eastern lake (46.07
ng/g) > western lake (39.38 ng/g) > central lake (30.88 ng/g). The concentration of OCPs
remained steady from May to July and reached a maximum value in August, then fell rapidly
in September and continued to decrease from September to November. Seasonal trends in the
HCH and DDT contents were different. Specifically, the concentration of HCHs increased
slightly from spring to autumn, while the maximum concentration of DDTs was observed in
the summer, which was higher that of the other two seasons (Fig.1).
Composition of OCPs in the SPM
HCHs and DDTs were the two dominant OCPs. DDTs were the most dominant OCPs in
the spring and summer, and its proportion reached a maximum value in the summer (87.92%)
and decreased to a minimum in the fall (33.38%). The dominant OCPs in the fall was HCHs,
and its proportions in the spring, summer and fall accounted for 8.95%, 4.08% and 43.85%,
respectively. The proportion of HCB also reached a maximum (10.51%) in the fall. In
contrast, the proportion of the rest OCPs in all three seasons were lower than 10%.
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85
Fig. 1. temporal-spatial variations of OCPs, HCHs, DDTs and HCB in the SPM
Source apportionment of major OCPs in the SPM
The possible sources of major OCPs can be identified by looking at the isomer ratios of
these pesticides (Iwata et al. 1995). The ratios of α-/γ-HCH and β-/(α+γ)-HCH indicated that
the recent use of lindane was the primary source of HCHs in the SPM. The ratios of o,p’-
/p,p’-DDT and DDT/(DDD+DDE) indicated that residual DDTs in SPM were mainly derived
from the new inputs of industrial DDT. The α-/γ-chlordane ratio of most samples was less
than 0.77, indicating that there was a recent input of industrial chlordane in Lake Chaohu.
Potential ecological risk
The Consensus-Based Sediment Quality Guidelines (CB-SQGs) (MacDonald et al., 2000)
were used to evaluate the potential ecological risk of OCPs in the SPM. The results showed
that γ-HCH, p,p’-DDE and ΣDDTs might have a negative impact on aquatic organisms, and
that p,p’-DDT and o,p’-DDT had the greatest risks.
CONCLUSIONS
Seventeen types of OCPs were detected in the SPM samples. HCHs and DDTs were found
as two dominant OCPs and with high residual levels. Their possible sources were the recent
illegal use of lindane and industrial DDT. HCHs and DDTs might have adverse effects on
aquatic organisms.
ACKNOWLEDGEMENTS
The funding was provided by the National Science Foundation of China (NSFC)
(41030529 and 40725004).
REFERENCES Iwata H, Tanabe S, Ueda K, Tatsukawa R (1995) Persistent organochlorine residues in air, water, sediments,
and soils from the Lake Baikal region, Russia. Environmental Science & Technology 29:792–801
MacDonald DD, Ingersoll CG, Berger TA (2000) Development and evaluation of consensus-based sediment
quality guidelines for freshwater ecosystems. Archives of Environment Contamination and Toxicology 39:20-31
Tao S, Liu WX, Li Y, Yang Y, Zuo Q, Li BG, Cao J (2008) Organochlorine pesticides contaminated surface soil
as reemission source in the Haihe Plain, China. Environmental Science & Technology 42:8395-8400
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86
Using stable isotope analysis in vegetated flow-through stream
mesocosms to study aquatic-terrestrial subsidies (O.104)
Matthias V. Wieczoreka, Denise Kötter
a, René Gergs
a and Ralf Schulz
a
aInstitute for Environmental Sciences, Fortstraße 7, Landau, 76829, Germany
INTRODUCTION
Emergence of aquatic insects provides a considerable energy subsidy to riparian food
webs but may also serve as a vector for contaminant residues (Walters 2008). Therefore
riparian food webs are at risk to be adversely affected by aquatic contamination. The
objective of the present study was to develop an integrated stream mesocosms test design
capable of identifying these inter-habit effects and, furthermore, providing a comprehensive
approach for current ecotoxicological testing within the scope of Regulation (EC) No.
1107/2009. We chose the widely distributed web-building spider Tetragnatha extensa as a
representative species for riparian predators. Trophic aspects of riparian food webs were
investigated by stable isotope analysis, carbon (δ13
C) and nitrogen (δ15
N).
METHODS
The present study was performed at 4 of the 16 stream mesocosms at the University
Koblenz-Landau, Campus Landau (Germany). Each stream channel is 45 m long and 0.4 m
wide. The channels contained a sediment layer of 9 cm consisting of sieved top soil and were
equipped with the helophyte Berula erecta. The mesocosm system was run in recirculation
mode with flow rates up to 3 L/s. Meshed cages were placed above the vegetated stream
mesocosms each comprising a strip of a terrestrial model meadow ecosystem and a part of the
respective aquatic stream section. Four individuals of T. extensa were placed in each meshed
cage for a time period of one month. For qualitative and quantitative determination of
emerging insects, emergence tents were placed above the stream mesocosms and additional
meadow strips and were sampled in 48 – 72 h intervals and stored at -18°C. Subsequent to
taxonomic determination, stable isotope ratios of δ13
C and nitrogen δ15
N were measured in
spiders and their potential prey, including aquatic and terrestrial insects. Data analysis was
performed with R (package: SIAR).
RESULTS AND DISCUSSION
The analysis of stable δ13
C and nitrogen δ15
N isotope ratios revealed the trophic
relationships of the present stream mesocosm community, comprising emerging terrestrial
and aquatic insect species and the predatory spider T. extensa. Data analysis of prey and
spider samples showed that the overall emergence predominantly consisted of aquatic
emergence (>70 %). Stability and reproducibility in general were shown for the present
stream mesocosms. The test system was stable regarding abiotic water parameters and no
significant differences in community composition of the four mesocosms were observed
(PERMANOVA).
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87
Figure 1. δ
13C and δ
15N values (mean ± SD) of terrestrial and aquatic arthropods. Each replicate of
aquatic arthropods (n = 8) is composed of at least one individual. The replicates of T. extensa (n = 8) are
composed of 18 individuals with minimum of one individual per replicate. Due to low terrestrial
emergence, δ13
C and δ15
N values are composed of reduced replicates: Staphylinidae (n = 3), Empididae (n
= 3), Tipulidae (n = 4) and Cicadellidae (n = 8) with at least 3 individuals per replicate.
CONCLUSION
Evaluation of the present study indicates that the use of stable isotopes ratios in
ecotoxicological stream mesocosm studies can provide a tool to identify contaminant related
effects of aquatic pollution on riparian food web structure. Therefore, the inclusion of land-
water interactions such as trophic cross-ecosystem linkages in ecotoxicological stream
mesocosm studies might be a relevant future application to obtain and create more realistic
test scenarios.
ACKNOWLEGEMENTS
We thank various academic staff of the Institute for Environmental Sciences who
performed the stable isotope analysis and supported use over the whole experimental phase
and the data analysis.
REFERENCES Walters, D. M., K. M. Fritz, and R. R. Otter. 2008: The dark side of subsidies: adult stream insects export
organic contaminants to riparian predators. Ecological Applications 18:1835–1841.
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88
Mechanisms controlling metal/metalloid accumulation in organic
rich sediments (O.3)
Jörg Schallera
aInstitute of General Ecology and Environmental Protection, University of Technology
Dresden, PF 1117, 01737 Tharandt, Germany. Email: [email protected]
INTRODUCTION
Organic sediments are known to be a significant sink of inorganic elements and metal
pollutants in contaminated ecosystems. Metal / metalloid content of detritus has been shown
to increase significantly during decomposition. However the role of the decomposer
community in this fixation and the factors that make sediments a sink of metals and
metalloids remains unclear. Furthermore, the possible effect of nutrients availability during
decay and especially the availability of silicon on metal fixation is not fully understood.
Consequently, we made experiments to test these factor in regard to their impact to metal
fixation.
METHODS
Laboratory batch experiments were conducted to assess the effect of different functional
groups of invertebrates and different litter types (grown under high and low silicon
availability) on metal fixation during litter decomposition.
RESULTS AND DISCUSSION
During decomposition, invertebrate shredder as an ecosystem engineer significantly
facilitated the enrichment of magnesium (250%), manganese (560%), cobalt (310%), copper
(200%), zinc (43%), arsenic (670%), cadmium (100%) and lead (1340%) into small particle
sizes. The enrichments occurred under very high concentrations of dissolved organic carbon.
Smaller particles have higher surface area that results in higher biofilm development. Further,
the highest amounts of elements were observed in biofilms. Therefore, invertebrate shredders
can enhance retention of large amounts of metal and arsenic in wetlands. Furthermore, we
found clear effects of bioturbators like the tube dwelling Chironomus plumosus.
In addition, the results of the silicon experiment are a significantly higher metal/metalloid
accumulation during decomposition of plant litter grown under low silicon availability
(Fig. 1). This may be explained by the altered litter properties (mainly nutrient content)
affecting the microbial decomposition of the litter, the microbial growth on the litter and
possibly by the silicon double layer, which is evident in leaf litter with high silicon content
and reduces the binding sites for metals/metalloids. Furthermore, this silicon double layer
may also reduce the growing biofilm by reducing the availability of carbon compounds at the
litter surface and has to be elucidated in further research. Hence, low silicon availability
during plant growth enhances the metal/metalloid accumulation into plant litter during
aquatic decomposition.
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89
Fig. 1. Effect of silicon availability on metal fixation during litter decay from Schaller (2013).
CONCLUSIONS
In conclusion, the process of litter decay controls the metal fixation by organic matter.
This effect is enhanced by invertebrate shredder. Bioturbators as another functional animal
group significantly affect the remobilization/fixation of metals within organic rich sediments.
In addition, silicon availability during plant growth impact the metal fixation during decay of
the plant material as a part of organic rich sediments.
REFERENCES Schaller, J. 2013. Metal/metalloid fixation by litter during decomposition affected by silicon availability during
plant growth. Chemosphere 90:2534-2538.
ABSTRACTS - WETPOL 2013 - October 13-17, 2013 - Nantes - FRANCE
90
Mining wastewater treatment by steel slag reactive filters (O.57)
Yves Comeaua, Dominique Claveau-Mallet
a, Scott Wallace
b
aPolytechnique Montréal, P.O. box 6079, Station Centre-Ville, Montreal (QC) CANADA
H3C 3A7 ([email protected]; [email protected])
bNaturally Wallace Consulting, 109 E. Myrtle Street, Stillwater, MN 55082, USA
INTRODUCTION
Management of closed mining sites is a major environmental issue. In particular, mining
leachates produced from contaminated rain and surface water have to be treated before being
discharged. In this project, we were interested in the orphan Joplin gypsum mine, located in
Missouri. The current lime precipitation system is deficient and discharge criteria for
phosphorus, fluoride and metals are not met. The objective of the project was to propose a
replacement treatment system that would be efficient and economical. The tested system was
a steel slag constructed wetland. It was previously shown that steel slag removes efficiently
phosphorus (Drizo et al., 2006; Vohla et al., 2011), but its utilization for the treatment of
multi-components wastewater remains not well documented. Limitations concerning the use
of slag filters are high pH at the effluent, clogging and a sharp decline in efficiency
(Chazarenc et al., 2008).
METHODS
Lab-scale tests were conducted using slag filters and synthetic mining wastewater.
Plexiglas columns (length 17 cm and diameter 15 cm) were bottom fed with two synthetic
wastewaters representing diluted and concentrated leachates. The wastewater composition
was pH 6.9-5.7, Al 1.7-8.2 mg/L, Mn 0.24-0.83 mg/L, Zn 0.20-3.3 mg/L, o-PO4 11-107 mg
P/L and F 9-37 mg/L. Two types of slag were tested: electric arc furnace (EAF) slag from
Fort Smith, Arkansas and EAF slag from Blytheville, Arkansas. Void hydraulic retention
time (HRTV) of columns was between 4.3 and 19.2 h. Water was sampled at the outlet of
columns and analysed for pH, phosphorus, fluoride, calcium, manganese, zinc and
aluminium. Precipitates formed in filters were sampled at the end of tests and analysed by X-
ray diffraction for composition and crystal size. A schematic of the experimental system is
presented in Figure 1.
Fig. 1. Schematic of the experimental setup.
Fort Smith Blytheville
Type of Upstream Downstream Duration
wastewater columns columns (d)
High
conc.
3A
HRTV = 14.5 h
3B
HRTV = 17.3 h169
Type of slag
1A
HRTV = 14.2 h
1B
HRTV = 18.2 h162
Low
conc. 4A
HRTV = 4.8 h
4B
HRTV = 4.3 h145
5A
HRTV = 19.2 h
5B
HRTV = 14.6 h179
2A
HRTV = 17.2 h
2B
HRTV = 17.2 h222
ABSTRACTS - WETPOL 2013 - October 13-17, 2013 - Nantes - FRANCE
91
RESULTS AND DISCUSSION
Simultaneous removal of phosphorus, fluoride and metals by a slag filter was shown to be
possible and efficient. The best system was composed of two successive Fort Smith slag
filters with a total HRTV of 34 hours. Its overall removal was 99,9%, 85.3%, 98.0% and
99.3% for P, F, Mn and Zn, respectively. The system was efficient for the whole test duration
(179 days), however, a decrease in efficiency and pH was observed after 70 days in the
upstream column.
Fig. 2. Influent and effluent concentration from two successive Fort Smith slag filters operated at total
HRTV of 34 h.
Phosphorus and metals removal was related with a high pH in the effluent. Fluoride
removal was also related to high pH in the effluent but also to the F/P ratio in the wastewater.
With a high F/P ratio (0.88 by mass), soluble fluoride was in excess for the precipitation of
fluoroapatite, reducing the fluoride removal efficiency (10%). Fluoride removal was higher
(85%) at lower F/P ratio (0.33 by mass). Fluoride was removed more efficiently by the
Blytheville slag (>90%) then by the Fort Smith one (75%).
The proposed mechanism for P removal was precipitation of apatite and crystal growth.
Apatite growth rate was related to the phosphorus concentration in the wastewater. Calcite
crystals growth was identified as a competing mechanism to P removal (Claveau-Mallet et
al., 2013).
CONCLUSIONS
A constructed wetland composed of Fort Smith EAF slag was suitable for the treatment of
a mining wastewater containing a high concentration of phosphorus (as much as 110 mg
P/L), fluoride and metals.
Fluoride removal in slag filters was favoured by a low F/P ratio in the wastewater.
Apatite crystal growth was the main P removal mechanisms in steel slag filters.
REFERENCES Chazarenc, F., Kacem, M., Gerente, C. and Andres, Y. (2008) 'Active' filters: a mini-review on the use of
industrial by-products for upgrading phosphorus removal from treatment wetlands. 11th
Conference on Wetland
Systems for Water Pollution Control, November 1-7. Indore, India, International Water Association.
Claveau-Mallet, D., Wallace, S. and Comeau, Y. (2013). Removal of phosphorus, fluoride and metals from a
gypsum mining leachate using steel slag filters. Water Research. 47(4): 15-12-1520.
Drizo, A., Forget, C., Comeau, Y. and Chapuis, R. (2006) Phosphorus removal by steel slag and serpentinite.
Water Research. 40(8): 1547-1554.
Vohla, C., Koiv, M., Bavor, H. J., Chazarenc, F. and Mander, U. (2011). Filter materials for phosphorus
removal from wastewater in treatment wetlands - A review. Ecological Engineering. 37(1): 70-89.
0.0001
0.001
0.01
0.1
1
10
100
PO4-P F Mn Zn Al
co
ncen
etr
ati
on
(m
g/L
)
PO4-P
ABSTRACTS - WETPOL 2013 - October 13-17, 2013 - Nantes - FRANCE
92
Metals removal in 8 different configurations of horizontal
constructed wetlands (O.60)
Anna Pedescollab
, Ricardo Sidrach-Cardonab, Eloy Bécares
a
a Ecology Section, Department of Biodiversity and Environmental Management, University
of León, Campus de Vegazana s/n, 24071 León, Spain ([email protected]).
b Environmental Institute, c/ La Serna 56, 24007 León, Spain.
INTRODUCTION
Although constructed wetlands (CWs) are a suitable technology for wastewater treatment,
mainly in small communities (García et al., 2010), we still know little about the behaviour of
these systems. In this work we tried to understand how these systems work depending of its
design configuration, by means the analysis of metal removal.
METHODS
Eight mesocosms-scale CWs were built inside the facilities of the León WWTP, in the
Northwest of Spain. Each CW consisted of a fibreglass container measuring 80 cm wide, 130
cm long and 55 cm high, which differed from each other in the design configuration.
Characteristics of the CWs are listed in Table 1. The experimental plant was operated from
May 2007 to December 2010. The wetlands were fed with homogenised wastewater from the
primary settler of the León WWTP at a hydraulic loading rate of 50 mmd-1
(CW6’ received
100 mmd-1
) with a continuous flow rate. Table 1. Main characteristics of the wetlands of the experimental plant.
CW Plant species Flow type
Gravel
matrix
(cm)
Water
depth
(cm)
Outlet
pipe
position
Organic load
(g BOD5m-2
d-1
)
CW1 Typha
angustifolia
Hydroponic (Floating
macrophytes)
Without
gravel 30 Top 3-10
CW2 Typha
angustifolia
Free water surface
(FWS) 25 50 Top 3-10
CW3 Typha
angustifolia FWS 25 50 Bottom 3-10
CW4 Unplanted FWS 25 50 Bottom 3-10
CW5 Phragmites
australis
Hydroponic (Floating
macrophytes)
Without
gravel 30 Bottom 3-10
CW6 Phragmites
australis Subsurface flow (SSF) 50 45 Bottom 3-10
CW6’ Phragmites
australis SSF 50 45 Bottom 6-20
CW7 Unplanted SSF 50 45 Bottom 3-10
Samples of inlet and outlet were taken in summer and winter campaigns and analysed for
different metals concentration (Fe, As, Ni and Pb).
RESULTS AND DISCUSSION
The experimental plant was efficient in Pb removal (with efficiencies ranging from 79% to
92%). Effluent concentrations were in the range of other studies for all the metals (Lesage et
al., 2007) although differences were observed between CWs depending on the metal analysed
(Fig. 1). Thus, strict subsurface flow systems (CW6, CW6’ and CW7) were less efficient in
Fe and As removal. In fact, these systems released Fe and As, which can be related with
ABSTRACTS - WETPOL 2013 - October 13-17, 2013 - Nantes - FRANCE
93
redox conditions within the wetlands (Galletti et al., 2010; Lesage et al., 2007). SSF wetlands
were more reduced than FWS systems (CW2, CW3 and CW4).
Fig. 1. Metals concentration for the influent and for outlet samples of the experimental plant for winter
and summer campaigns. Concentrations are expressed in gL-1
.
Moreover, clearly differences were observed between winter and summer sampling
campaigns. Also redox conditions presented seasonality because of the higher plant and
microbial activity in summer (García et al., 2010).
CONCLUSIONS
Metals analysed in this study seemed to be more affected by flow type (FWS and
hydroponic vs. SSF) and seasonality than other design factors, such as plant species or the
gravel matrix. In this sense, FWS flow would be more suitable conditions for metal removal,
due to the more oxidised conditions within these systems.
ACKNOWLEDGEMENTS
This study was funded by the Spanish Ministry of Science through the projects CTM2005-
06457-C05-03 and CTM2008-06676-C05-03/TECNO. Anna Pedescoll acknowledges the
Juan de la Cierva Programme of the Spanish Ministry of Science and Innovation.
REFERENCES Lesage, E., Rousseau, D.P.L., Meers, E., Tack, F.M.G., De Paw, N. (2007) Accumulation of metals in a
horizontal subsurface flow constructed wetlands treating domestic wastewater in Flanders, Belgium. Science of
the Total Environment 380, 102-115.
Galletti, A., Verlicchi, P., Ranieri, E. (2010) Removal and accumulation of Cu, Ni and Zn in horizontal
subsurface flow constructed wetlands: Contribution of vegetation and filling medium. Science of the Total
Environment 408, 5097-5105.
García, J., Rousseau, D.P.L., Morató, J., Lesage, E., Matamoros, V., Bayona, J.M. (2010) Contaminant removal
processes in subsurface flow constructed wetlands: A review. Critical Reviews in Environmental Science and
Technology 40(7), 561-661.
Inf CW1 CW2 CW3 CW4 CW5 CW6 CW6' CW7
As
0
5
10
15
20
25
30
Inf CW1 CW2 CW3 CW4 CW5 CW6 CW6' CW7
Fe
0
10000
20000
30000 Winter
Summer
Inf CW1 CW2 CW3 CW4 CW5 CW6 CW6' CW7
Ni
0
5
10
15
20
25
Inf CW1 CW2 CW3 CW4 CW5 CW6 CW6' CW7
Pb
0
2
4
6
8
10
ABSTRACTS - WETPOL 2013 - October 13-17, 2013 - Nantes - FRANCE
94
Pharmaceuticals in a Subsurface Flow Constructed Wetland and
Two Ponds (O.128)
S. Rühmlanda, A. Wick
b, T.A. Ternes
b, M. Barjenbruch
a
aTechnische Universität Berlin, Department of Urban Water Management FG Siedlungswasserwirtschaft, Sekr.
TIB 1-B16, Gustav-Meyer-Allee 25, Berlin, 13355, GERMANY www.siwawi.tu-berlin.de
bFederal Institute of Hydrology, Department of Water Chemistry, Am Mainzer Tor 1, Koblenz, 56068,
GERMANY ([email protected]; [email protected])
INTRODUCTION
Micropollutants can have an impact on ecosystems. For example, the antimicrobial
Sulfamethoxazole (SMX) is able to alter the composition of microbial communities and
hinder their nitrate reduction capacity at concentrations as low as 1.3 µg/L (Underwood et al.
2011). Constructed wetlands and ponds provide various options for the elimination
(degradation, absorption) of pharmaceuticals. This study examinates the treatment
performance of three different designs at a technical scale with emphasis on the redox
conditions.
METHODS Layout of Constructed Wetland (CW) and Ponds
The CW and the ponds were built and planted in 2004 and 2005. They are fed with the
same effluent from a large conventional wastewater treatment plant with nutrient removal in
the outskirts of Berlin in Germany. The hydraulic loading was 50 mm/d. The following
treatment plants were examined:
•Sandy SSF: sandy subsurface flow wetland, 1,320 m², water level constantly above filter
bed, estimated HRT = 11 d, O2 = 0.2 mg/l, redox potential = -150 mV
•Pond with floating plants: floating aquatic plant system, planted with Iris pseudacorus,
Scirpus sp. and Carex sp., 1,520 m², estimated HRT = 5.5 d, O2 = 0.2 mg/l, redox potential =
-140 mV
•Unplanted pond, 1,550 m², estimated HRT = 4 d, O2 = 2.2 mg/l, redox potential = -30 mV
The oxygen concentrations and redox potentials given above are the averages of five
measurements at the outlets in August 2012. Sampling and Analysis
The influent was sampled four times with an automatic sampler for 24 hours each. Seven
grab samples were taken at the effluents of the three cells. Sampling took place between
August 13th and August 31st 2012. The weather was dry in general and the air temperature
was around 20°C during the day.
The samples were filtered through 0.45 µm syringe filters made of regenerated cellulose
and a surrogate mix was added to a final concentration of 200 ng/L. The samples were
analysed by direct injection with a LC-MS/MS system (QTrap® 5500, AB Sciex, Darmstadt,
Germany). The injection volume was 80 µL and the chromatographic separation was
achieved using a Zorbax Eclipse Plus C-18 (2.1 x 150 mm, 3.5 µm, Agilent Technologies,
Waldbronn, Germany). All target compounds were measured within one chromatographic run
by scheduled multiple reaction monitoring (sMRM) using electrospray ionization (ESI) both
in negative and positive mode. At least two mass transitions were measured for quantification
and confirmation. An internal standard calibration was used for quantification. For quality
ABSTRACTS - WETPOL 2013 - October 13-17, 2013 - Nantes - FRANCE
95
assurance samples were also fortified with the target compounds at a level of 200 ng/L and
1000 ng/L. Results were only considered valid if the recovery was in the range of 75-125%.
RESULTS AND DISCUSSION
Consistent with their known persistence, the antiepileptic carbamazepine (CBZ) and the
artificial sweetener acesulfame were not significantly removed (<25%) by the three different
treatment systems. However, for 40 of the 53 measured target compounds a significant
removal of >30% could be observed at least for one of the treatment systems. For example,
diclofenac was diminished from 2.2 to 0.3 µg/L in the unplanted pond, which corresponds to
a removal of 82 ± 4% (see table). The pond with floating plants and the SSF showed lower
removal efficiencies of 65 ± 8 and 20 ± 19%, respectively. As diclofenac is a compound
known to be sensitive to photochemical degradation (Poiger et al., 2001), the different
removal efficiencies of diclofenac in the three treatment systems might be caused by their
different exposure to sunlight.
Table. Influent concentrations [µg/L] and elimination efficiencies of the treatment systems
subsurface flow wetland (SSF), pond with floating plants and unplanted pond
The results for other micropollutants also revealed that the removal efficiencies strongly
depend on the specific treatment system. For example, the results indicated that the good
supply with oxygen (oxic biodegradation) and/or light (photochemical degradation) in the
unplanted pond significantly enhanced the conversion of venlafaxine (VLX), VLX-
metabolites, CBZ-metabolites and the betablocker metoprolol. Gasser et al. (2012) made the
same observations for VLX and its metabolites. On the other hand, very low redox potentials
seem to be favourable to remove SMX which is also consistent with results of Mohatt et al.
Compound
Influent, n=4
Treatment Cell
Elimination, n=7
concentration
[µg/L]
95% confidence
interval [%] [%]
statistical
error [%]
Diclofenac 2.2 18 SSF 20 19
(analgesic) Pond floating pl. 65 8
Pond 82 4
Carbamazepine (CBZ) 2.2 9 SSF ≤0 16
(antiepileptic) Pond floating pl. 15 17
Pond ≤0 11
2-Hydroxy-CBZ 0.21 10 SSF 9 16
(CBZ-metabolite) Pond floating pl. 35 14
Pond 65 5
3-Hydroxy-CBZ 0.27 16 SSF ≤0 27
(CBZ-metabolite) Pond floating pl. 34 16
Pond 79 4
Venlafaxine (VLX) 0.50 10 SSF 53 9
(antidepressant) Pond floating pl. 76 5
Pond 81 3
N-Desmethyl-VLX 0.12 13 SSF 49 9
(VLX-metabolite) Pond floating pl. 60 9
Pond 72 4
O-Desmethyl-VLX 1.7 14 SSF 24 14
(VLX-metabolite) Pond floating pl. 48 13
Pond 83 5
N,O-Didesmethyl-VLX 0.33 15 SSF 15 17
(VLX-metabolite) Pond floating pl. 39 15
Pond 75 7
Sulfamethoxazole (SMX) 0.32 36 SSF 60 15
(sulfonamide antibiotic) Pond floating pl. 53 20
Pond 30 26
∑ SMX, Acetyl-SMX 0.46 22 SSF 70 7
Pond floating pl. 61 12
Pond 44 12
Metoprolol 2.0 7 SSF 64 5
(betablocker) Pond floating pl. 73 4
Pond 92 3
ABSTRACTS - WETPOL 2013 - October 13-17, 2013 - Nantes - FRANCE
96
(2011). While the concentration of SMX (including the conjugate acetyl-SMX) decreased by
70 ± 7% in the SSF, SMX was only removed by 44 ± 12% under more aerobic conditions in
the uncovered pond.
CONCLUSION
Constructed wetlands and ponds are able to further diminish certain micropollutants
following a municipal wastewater treatment plant. The design of the treatment system
determines whether degradable compounds under anaerobic or under aerobic conditions are
removed.
REFERENCES Gasser, G.; Pankratov, I.; Elhanany, S.; Werner, P.; Gun, J.; Gelman, F.; Lev, O. (2012) Field and laboratroy
studies of the fate and enantioneric enrichment of venlafaxine and O-desmethyolvenlafaxine under aerobic
and anaerobic conditions. Chemosphere 88:98–105.
Mohatt, J., Hu, L., Finneran, K., Strathmann, T. (2011) Microbially Mediated Abiotic Transformation of the
Antimicrobial Agent Sulfamethoxazole under Iron-Reducing Soil Conditions. Environmental Science &
Technology 45:4793-4801.
Poiger, T., Buser, H.-R., Müller, M. (2001) Photodegradation of the pharmaceutical drug diclofenac in a lake:
pathways, field measurements, and mathematical modeling. Environ. Toxicol. Chem. 20(2):256-263.
Underwood, Jennifer C.; Harvey, Ronald W.; Metge, David W.; Repert, Deborah A.; Baumgartner, Laura K.;
Smith, Richard L. (2011) Effects of the Antimicrobial Sulfamethoxazole on Groundwater Bacterial
Enrichment. Environment Science and Technology 45:3096–3101.
ABSTRACTS - WETPOL 2013 - October 13-17, 2013 - Nantes - FRANCE
97
Phragmites sp. Ability to Conjugate Alachlor (O.137)
Renata Ferreiraa, Vanessa Romon
b, Magda Fernandes
a, Augusto Etchegaray
b,
Susete Martins-Diasa
a Institute for Biotechnology and Bioengineering, Centre of Biological and Chemical Engineering, Department
of Bioengineering, Instituto Superior Técnico, Av. Rovisco Pais, 1049-001 Lisboa, PORTUGAL
([email protected] - [email protected] - [email protected])
b Faculty of Chemistry, PUC-Campinas, Rod. D. Pedro I, Km 186, Campinas, SP, 13086-900, BRAZIL
([email protected] - [email protected])
INTRODUCTION
The extent of herbicides routinely applied in agricultural intensely augmented over the
years and consequently, environmental and human health risks also increased. Constructed
wetlands (CWs) have been used as a cost-effective and sustainable treatment method for the
retention and degradation of organic contaminants in agricultural ecosystems (Kadlec and
Wallace, 2009). Plants are unique organisms equipped with notable metabolic and absorption
skills, along with transport systems that can take up nutrients or contaminants selectively
from the growth matrix, soil or water. Following uptake, the lipophilic xenobiotic is
converted into a more water-soluble and less toxic metabolite that can therefore be
eliminated. Glutathione S-transferases (GSTs) are a family of isozymes that catalyse the
conjugation of glutathione to several xenobiotics and thus play a central role in detoxification
mechanisms of eukaryotes and prokaryotes. In plants, these enzymes gained particular
attention with respect to detoxification of herbicides. Alachlor is an herbicide from the
chloroacetanilide family that is widely used for the control of annual grasses and broadleaf
weeds in a variety of major crops (e.g. maize, corn and soybeans). It is absorbed in the roots
and transferred to the upper parts of the plant through the apoplast, inhibiting the elongation
of the root system and the development of the shoots of young plants (Labrou et al., 2005).
While integrated in CWs, Phragmites should play an important role on phytoremediation
of domestic, agricultural and industrial wastewaters. The aim of the present work was to
evaluate Phragmites sp. ability to conjugate alachlor, and therefore contribute to the
understanding and potential use of reed plants in CWs for the treatment of agriculture runoff.
METHODS
Phragmites leaves were collected from a pilot-scale horizontal flow constructed wetland
that had been fed with tap water, installed at IST university campus, and immediately frozen
in liquid nitrogen. The plant material was ground to powder in a pre-cooled mortar using a
pestle under liquid nitrogen. Protein crude extract (CE) was prepared according to Davis and
Swanson (2001). A control of GST activity was measured using 10g of CE and 1-chloro-
2,4-dinitrobenzene (CDNB,1.6mM) and reduced glutathione (GSH, 20mM) as substrates.
The CDNB conjugate formation was followed at 340nm (9.6 mM-1
cm-1
) for 250 sec, at
25ºC. One unit (U) of GST specific activity was defined as 1mol of CDNB conjugated per
minute per g of protein. Alachlor conjugation reaction was accomplished using 141g of CE,
0.5mM GSH and 0.25mM alachlor. After incubation at 25ºC for 30 min, the reaction was
ended by adding 12L of 0.6M HCl and the precipitated proteins were removed by
centrifugation (12000×g, 5 min). Reactions without CE were used as blank. Alachlor-
glutathione conjugation reaction was followed by High Performance Liquid Chromatography
with Diode-Array Detection (HPLC-DAD) using a ZORBAX Eclipse XDB-C18 column
(4.6×150mm, 5m diameter). The column was eluted as described by Hatton et al. (1996) for
28 min. The eluent was monitored for UV absorbance at 220 (conjugation formation) and
ABSTRACTS - WETPOL 2013 - October 13-17, 2013 - Nantes - FRANCE
98
264nm ( maximum of alachlor). After each run, the column was washed with acetonitrile for
12 min.
RESULTS AND DISCUSSION
Glutathione conjugation with alachlor is catalysed by GST. In Phragmites leaves CE, GST
was active (198 ± 25 U). The obtained results presented specific activity levels similar to
previous studies (Carias et al., 2008). HPLC elution profiles are presented in Fig. 1. At
220nm, the increase of the peak at the retention time of 2.3 min is due to the addition of CE
(presence of more peptide bonds). The existence of a new peak, found at 22.5 min, was
indicative of alachlor-GS formation. Alachlor was consumed by the enzyme, as showed in
the chromatogram at 264 nm, by the reduction of the herbicide peak at 2.7 min.
Fig. 1. HPLC chromatograms of the reaction of alachlor and GSH with Phragmites leaf enzymatic crude
extract, monitored at = 220 nm and = 264 nm. Control - without Phragmites crude extract.
CONCLUSIONS
In the present work, GST extracted from Phragmites leaves were able to conjugate with
the herbicide alachlor. This work is a step forward in order to understand reed plants
tolerance towards chloroacetanilide herbicides. It may be concluded that Phragmites can
minimize the toxic effects of agriculture runoff contaminated with herbicides.
ACKNOWLEDGEMENTS
The authors acknowledge support from the Fundação para a Ciência e a Tecnologia
(PTDC/AAC-AMB/112032/2009).
REFERENCES Carias, C.C., Novais, J.M. and Martins-Dias, S. (2008) Are Phragmites australis enzymes involved in the
degradation of the textile azo dye acid orange 7? Bioresource Technol. 99:243-251.
Davis, D.G. and Swanson, H.R. (2001) Activity of stress-related enzymes in the perennial weed leafy spurge
(Euphorbia esula L.). Environ. Exp. Bot. 46:95-108.
Hatton, P.J., Dixon, D., Cole, D.J. and Edwards, R. (1996) Glutathione Transferase Activities and Herbicide
Selectivity in Maize and Associated Weed Species. Pesticide Science. 46:267-275.
Kadlec, R.H. and Wallace, S.D. (2009) Treatment Wetlands. CRC Press Boca Raton, Florida. 1016p.
Labrou, N., Karavangeli, M., Tsaftaris, A. and Clonis, Y. (2005) Kinetic analysis of maize glutathione S-
transferase I catalysing the detoxification from chloroacetanilide herbicides. Planta. 222:91-97.
ABSTRACTS - WETPOL 2013 - October 13-17, 2013 - Nantes - FRANCE
99
Effect of hydrolysed polyacrylamide polymer contaminated oil
production water on batch-loaded surface flow wetland
mesocososms (O.142)
Stephane Prigenta, Tom Headley
b, Mitchell Kirby
a, James Johnston
a, Badar Al
Sharjib, Nasser Al-Azri
b, Roman Breuer
a
aBauer Nimr LLC P.O. Box 1186, Postal code 114, Al Mina Sultanate of Oman ([email protected] –
bPetroleum Development of Oman LLC, PO Box 81, Muscat, PC 100, Sultanate of Oman
INTRODUCTION
The Nimr Water Treatment Plant (NWTP) has been designed and built by the company
BAUER Nimr LLC in partnership with Petroleum Development Oman (PDO) for petroleum
produced water treatment in the southern desert of Oman. This treatment system has been
operating since 2010 and consists of a surface flow constructed wetland (SFCW) of 350 ha
planted primarily with Phragmites australis. The injection of polymer, such as hydrolysed
polyacrylamide (HPAM), into the Nimr oil reserve is currently planned by PDO, Oman’s
national oil company, in the forthcoming years to augment oil production. There are several
concerns surrounding the potential impacts of HPAM-contaminated produced water on the
operation of the oil separator, SFCW and salt work of the NWTP. The present study,
therefore, aimed to determine the preliminary effect of the use of HPAM on water quality,
plant health, evaporation, evapotranspiration at the NWTP.
METHODS
This experiment was carried out in 0.7 m3 (A = 1.2 m
2, H = 0.6 m) mesocosms
constructed from Intermediate Bulk Containers. Each mesocososm was filled, from the
bottom to the top, with 10cm of a coarse drainage gravel (Ø 18mm-24mm), 5cm of a fine
aggregate (Ø 2mm-10mm) and 20cm of soil substrate. In each planted mesocosm, 20
individual Phragmites australis seedlings were planted on 23rd
July, 2012. Triplicate
mesocosms were operated according to a range of treatment factors, such as HPAM
concentration (0ppm, 200ppm and 500ppm) and planting status (planted and non-planted
except for 500ppm) as shown on Table 1. Table 1: Treatment combinations of the batch-loaded experiment (Code: [0 or 200 or 500 ppm HPAM],[p
for planted or np for non-planted])
The experiment was set up and operated over a period of 5 months (Aug-Dec 2012), near
the NWTP. Six-day batch feeding was performed with well water (6ppt TDS) adjusted with
20-ppm oil in water and different HPAM concentrations (0ppm, 200ppm and 500ppm).
Water quality was monitored from the 10 cm deep water column five hours after “top up”
Code HPAM (ppm) Plants
0 200 500 + -
0,6,np x x
0,6,p x x
200,6,np x x
200,6,p x x
500,6,p x x
ABSTRACTS - WETPOL 2013 - October 13-17, 2013 - Nantes - FRANCE
100
according to these following parameters: Conductivity (EC), pH, Dissolved Oxygen (DO),
Temperature, Total Dissolved Solids (TDS) and Oil-in-Water (OiW). Water loss was
measured every second day of operation before the mesocosms were topped up. The above
ground biomass was monitored according to a non-destructive method. Shoot height, shoot
density and leaf health were measured on three plant clumps selected at the beginning of the
experiment within the mesocosms. Statistical analysis was performed using a single factor
ANOVA test in Excel™.
RESULTS AND DISCUSSION
The oil in water concentration of all treatments decreased to less than 0.5 mg.L-1
(detection limit) by the end of the six-day batches. The polymer treated plants reach an
average above ground biomass of 1000 g.m-2
by the end of the study (Figure 1). The reason
for the observed increase in growth in the HPAM treated mesocosms is likely due to nitrogen
content of the HPAM, which acted as a fertiliser for the plants under the otherwise nutrient
poor conditions. However, the difference in above ground biomass harvested between the
treatments was not statistically significant.
Figure 2: Dry weight of above ground biomass estimated over the study period
Polymer exposure seemed to increase the rate of leaf necrosis, with the plants exposed to
500 ppm HPAM showing the highest leaf yellowing and necrosis (85% of leaf dead after 6
weeks). This leaf necrosis could be related to increased uptake of boron, manganese, zinc,
molybdenum and nickel leading to higher concentrations in the leaves of the plants exposed
to HPAM. During the experiment, the evaporation rate was similar for both treated and
untreated mesocosms. After three months of establishment, the planted mesocosms receiving
200 ppm of HPAM displayed a higher average evapotranspiration than untreated mesocosms
(9 + 0.5 mm.d-1
). However, these results were not significant due to the high natural
variability amongst the replicates.
CONCLUSIONS
Reed growth and evapotranspiration rates, in some replicates, increased in response to the
polymer. However, results were not consistent across all of the replicated mesocosms and
therefore did not yield statistically significant differences between treatments. This was partly
due to scale limitations of the small mesocosms and short timeframe of the study.
Furthermore, several limitations could be pointed out such as the immature age of the plants
at the beginning of the experiment and the feeding method (batch loading). Therefore, a long-
term experiment is needed in a full scale SFCW to get a comprehensive answer on the effect
of polymer on the NWTP.
ACKNOWLEDGEMENTS
The authors are grateful to Professor H. Brix on his support to the collection and reed
leaves analysis from the NWTP.
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101
Treatment of Refinery Effluent Using Vertical Subsurface
Constructed Wetlands: A Case Study in the Tropics (O.144)
Hassana Ibrahim Mustaphaa,c
, J. J. A. van Bruggenb, P. N. L. Lens
a
a Department of Environmental Engineering and Water Technology, Pollution Prevention and
Resource Recovery, UNESCO-IHE, Institute for Water Education, P. O. Box 3015, 2601 DA
Delft, The NETHERLANDS ([email protected]) b
Department of Water Science and Engineering, UNESCO-IHE, Institute for Water
Education, P. O. Box 3015, 2601 DA Delft, The NETHERLANDS (h.vanbruggen@unesco-
ihe.org) a Department of Environmental Engineering and Water Technology, Pollution Prevention and
Resource Recovery Core, UNESCO-IHE, Institute for Water Education, P. O. Box 3015,
2601 DA Delft, The NETHERLANDS ([email protected]) c Federal University of Technology Minna, Department of Agricultural and Bioresources
Engineering, P. M. B 65, Minna, Gidan Kwano Campus. NIGERIA
INTRODUCTION
Industrialization is a very important tool in every nation's economy, at present; it is the main
source of hazardous pollutant into water bodies (Akhavan et al., 2008), particularly in
developing countries where stringent discharge rules are not observed. Most of the people's
livelihood in the developing countries depends on river water for farming, fishing and for
domestic purposes and as sources of soil amendments and for irrigation purposes (Agbenin et
al., 2009). Untreated or partially treated industrial wastewater channeled into the environment
and used for agricultural purposes, for animal consumptions or other purposes pose
considerable environmental problems. Conventional methods are energy intensive and are
very expensive for developing countries to afford; likewise, these methods generate by-
products that are often toxic to both human and the environment and require further treatment
(Ojumu et al., 2005). Constructed wetland technologies may offer a lower construction and
maintenance cost for wastewater treatment, which is especially suitable for developing
countries, also most of the developing countries are found in the tropics where constructed
wetlands are suitable due to the high temperature which enhances biodegradation activity
(Kantawanichkul et al., 1999).
METHODS
This study was conducted at the Kaduna Refinery and Petrochemical Company, Kaduna
(Kaduna South, Nigeria), which lies between latitude 9 0 N and 12
0 N and Longitude 6
0E
and 9 0 E within the Northern guinea savannah ecological zone of Nigeria. The refinery
effluents were treated by chemical addition, clarification, oxidation, oil skimming, filtration
and evaporation before being discharged via drainages into Romi stream. The conducted
experiment was a two-phase experiment. The first phase consisted of characterization of the
primary treated refinery effluent and the second phase addressed constituents of concern in
the final discharged effluent by using artificial vertical subsurface flow constructed wetlands
(VSSF).
The primary treated effluents samples were collected once every month from the final
discharge channel from September, 2011 to December, 2012 for characterization in order to
obtain baseline information on the quality of wastewater discharged into the environment.
Standard methods for Examination of Water and Wastewater were used.
Two VSSF units and duplicates were constructed with 47 cm in diameter and 55 cm in
height. These were planted with Typha latifolia as an alternative to achieve treatment of
ABSTRACTS - WETPOL 2013 - October 13-17, 2013 - Nantes - FRANCE
102
effluents to non-hazardous levels. The media used was gravel; three different sizes were used
starting at the bottom with 25-36mm, middle portion with size range of 16-25 mm and the top
of the unit with 6-10 mm in size. The refinery effluents were fed gradually by gravity from a
5000 L tank into the wetland units at flow rate of 35L/day and hydraulic retention time of 7
days.
RESULTS
The discharged effluent from the refinery contained high levels of TSS ( 336 mg/l), BOD (
283 mg/l), COD ( 521 mg/l), turbidity (253 mg/l), ammonia (13 mg/l), phosphate (16 mg/l),
potassium (31 mg/l), Cd (0.03 mg/l), Cr (3.4 mg/l), Pb (0.06 mg/l), phenol (1.16µg/L ) and
oil and grease (14 mg/l) which were higher than the permissible discharge limits. There was a
good reduction in the concentration of BOD, COD, ammonia and turbidity with removal
efficiency of 75%, 67%, 51% and 83.98% for BOD, COD, ammonia and turbidity
respectively.
CONCLUSIONS
Typha planted vertical subsurface flow constructed wetlands units were able to reduce the
concentration of BOD, COD, ammonia and turbidity from secondary treated refinery
wastewater.
ACKNOWLEDGEMENTS
The author acknowledges the Netherlands Fellowship Program (NFP) for their financial
support. Dr. Ibrahim El-Idris and staff and management of Kaduna Refinery and
Petrochemical Company, Kaduna, Nigeria are also acknowledged for their support.
REFERENCES Agbenin J. O., Danko, M., and Welp, G (2009). Soil and vegetable compositional relationships of eight
potentially toxic metals in urban garden fields from northern Nigeria, J. Sci. Food Agric. 89:49-54
Akhavan, S. A., Dejban Golpasha, I., Emani, M and Nakhoda, A. M (2008). Isolation and characterization of
crude oil degrading Bacillus spp., Iran. J. Environ. Health. Sci. Eng., 5 (3):149-154
Ojumu, T. V., Beelo, O. O, Sonibara, J. A and Solomon, B .O (2005). Evaluation of microbial systems for
bioremediation of petroleum refinery effluents in Nigeria, African Journal of Biotechnology, 4 (1): 31-35
Kantawanichkul, S., Pilaila, S., Tanapiyawanich, W., Tikampornpittaya, W and Kamkrua, S (1999). Wastewater
treatment by tropical plants in vertical-flow constructed wetlands. Wat. Sci. Tech. 40 (3): 173-178.
ABSTRACTS - WETPOL 2013 - October 13-17, 2013 - Nantes - FRANCE
103
Storage of agricultural drained water by a pond / reservoir
system to reduce nitrate and pesticides transfer (O.147)
Tournebize J.a, Chaumont C.
a, Fesneau C.
a, Mänder Ü.
a
aIrstea, Hydrosystems and Bioprocesses Research Unit, 1 rue Pierre Gilles de Genes, F92761 Antony, FRANCE
([email protected] – [email protected] – [email protected])
INTRODUCTION
Agricultural non-point source pollution is of increasing concern as attested by the
implementation of new regulations like the European Water Framework Directive
2000/60/EC. To comply with these regulations, actions can be taken at different scales. At the
local scale, fertilizers and pesticide application rate reduction should first be implemented.
However, complementary actions at the watershed scale are needed since remaining applied
molecules will transfer from the watershed to natural receiving waters. Among them,
artificial wetlands including pond and reservoir are suspected to be able to provide nitrate and
pesticides mitigation. The aim of this study is to observe the efficiency of a pond/reservoir to
remove nitrate and pesticides from agricultural drainage water in intensive agricultural
catchment located in Ile de France region of France, over the period 2007-2012.
METHODS
A man-made pond and reservoir used as a constructed wetland for this study is located in
Aulnoy, France, 70 km northeast of Paris (figure 1). The pond and reservoir measure 860 and
3305 m2, respectively, and a total estimated storage volume of 10,000 m
3. The ratio between
the pond/reservoir surface and the agricultural catchment surface is 1.2%. The study site is
located inside the Orgeval catchment belonging to a water quality research observatory. The
climate is oceanic temperate with a mean annual temperature and precipitation of 12°C and
700mm respectively. The agricultural catchment of 33 hectares is located in the sedimentary
Paris Basin. The agricultural land is subsurface drained using perforated pipe installed 10m
apart and buried 0.8-1m to enable soil cultivation during winter. Cereals (corn, maize),
legumes (horse bean, pea), sugar beet or rape are the dominant crops grown in the region.
Drainage collector as inlet of pond/reservoir and outlet of pond/reservoir were equipped with
hourly water level sensor and a 90° V – notch sections and a weekly flow proportional
sampler. Over 30 pesticides were analysed during 5 years.
Figure 3. Experimental pond/reservoir location at outlet of a 33ha agricultural watershed belonging to
Orgeval Observatory (Seine et Marne, France)
0 40 km 0 200 m
33-ha agricultural
catchment totally
drained
Main drain
Orgeval catchment
Bec
k
N N
Pond
Spring
Overflow10 m
Reservoir
Outflow
Main drain
N
0 40 km 0 200 m
33-ha agricultural
catchment totally
drained
Main drain
Orgeval catchment
Bec
k
NN NN
Pond
Spring
Overflow10 m
Reservoir
Outflow
Main drain
NN
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104
RESULTS AND DISCUSSION
Nitrate concentration between inlet and outlet were reduced from an average value of
63mg/L to 23mg/L in the pond/reservoir system. Punctual investigations showed that
denitrification is the main dissipation process. Nevertheless N2 or N2O emissions were not
monitored to confirm or not the total denitrification reaction. In the whole about 50% of
nitrate fluxes were removed from the annual drained water.
Pesticides transfer depended strongly on farmer practices. Pesticides exportations from the
drained watershed were linked to date and applied amount over the crop as well as pesticides
properties (Koc and DT50). The average concentrations were slightly reduced, showing
nevertheless elevated concentration mitigation. It was not possible to determine if
degradation or simple dilution was the main process. In term of annual fluxes, some sorbing
pesticides showed 100% removal efficiency, whereas mobile pesticides less than 30%. Note
that 3 pesticides showed negative removal efficiency, highlighting a possible desorption
process.
The pond/reservoir system allowed storing about 14% of annual drained water. This high
volume led to a 300m3 per drained hectare ratio. In this context, hydraulic residential time
varied between few weeks during winter to months during summer. Removal efficiency
depended on seasonal variation as well. Global mitigations were about 50% and 46% for
nitrate and pesticides respectively. Those results are comparable with literature values.
Figure 4. Nitrate and pesticides concentrations at inlet and outlet of the pond/reservoir system during
2007-2012
CONCLUSIONS
A pond/reservoir system as buffer zone between agricultural land and surface water body
appeared to be a good complementary action to reduce nitrate and pesticides transfer by a
factor 2. Hydraulic residential time and temperature seemed to be the main parameters
controlling removal efficiency. Two questions remained unsolved yet dealing with GES
emissions from denitrification process for nitrate and desorption process for pesticides.
Should we wait before recommending this such land management helping to reduce nonpoint
source pollution from subsurface drained watershed?
Inlet Outlet
Pes
tici
de
Co
nce
ntr
ati
on
(µ
g/l
)
Inlet Outlet
ABSTRACTS - WETPOL 2013 - October 13-17, 2013 - Nantes - FRANCE
105
Behaviour of dimethylphenol isomers in the rhizosphere of
Juncus effusus (O.68)
L. Schultze-Nobre, A. Wiessner, U. Kappelmeyer, P. Kuschk
Department of Environmental Biotechnology, Helmholtz Centre for Environmental Research
- UFZ, Permoserstraße 15, Leipzig, D-04318, GERMANY ([email protected] -
[email protected] - [email protected] - [email protected])
INTRODUCTION
In future a renaissance of coal pyrolysis industry is predicted replacing the petrochemistry
resulting in the revival of new waste water treatment plants with new treatment methods.
Constructed wetlands (CWs) could be a relatively new option in the complex sequence of
physicochemical and biological treatment processes which are applied nowadays. We could
not found enough and consistently experimental results in the literature about 2,6-DMP
elimination in anaerobic process. Aim of the present study was to forecast the fate of
dimethylphenols (DMPs) as effluent constituents of coal pyrolysis and petrochemical
industries in CWs. Because of the low degradation potential under anaerobic condition
(Thomas and Lester, 1993; Puig-Grajales et al., 2000) models experiments were realized
simulating the root zone of horizontal subsurface-flow constructed wetlands where a mosaic
structure of aerobic and anaerobic zones can be expected (Winter and Kickuth, 1989)
METHODS
A laboratory-scale planted fixed bed reactor (PFBR) simulating the microgradient of
rhizosphere zone of constructed wetlands (Kappelmeyer et al., 2002;
Wiessner et al., 2005) planted with Juncus Effusus (see Fig. 1) is
established. The reactor was fed with synthetic wastewater containing a
mixture of 2,6-, 3,4- and 3,5- DMP-isomers in a equimolar ratio as the
only organic carbon contaminants. Experimental phases with different
inflow concentrations of total DMPs were investigated resulting in case of
the lower inflow concentration of 15.7 mg C/L aerobic and in case of the
higher inflow concentration of 78.7 mg C/L anaerobic conditions in the
soil pore water of the reactor. Fig. 1: PFBR
RESULTS AND DISCUSSION
In aerobic conditions Fig.2 - A,B and D
3,4, 3,5- and 2,6-DMP were almost eliminated
respectively.
In anaerobic condition Fig. 2 - D the
removal efficiency were less than in
aerobic condition
and the elimination rate worsened over
time. Better removal were founded by 3,4-
> 3,5- > 2,6-DMP.
Fig. 2: Data from long-term research of 3,4-, 3,5- and 2,6-DMP-C removal in a laboratory-scale PFBR
ABSTRACTS - WETPOL 2013 - October 13-17, 2013 - Nantes - FRANCE
106
CONCLUSIONS
We have successfully studied the elimination processes of 2,6-DMP under aerobic and
anaerobic conditions. Our long-term research findings shows that DMP can be removed in
aerobic and anaerobic operated conditions in a laboratory scale planted reactor system.
Better removal were obtained with 3,4- > 3,5- > 2,6-DMP. Our experimental results in
comparison with the literature shows that 2,6-DMP can be also removed by anaerobic
conditions using a PFBR.
ACKNOWLEDGEMENTS
This work was supported by the Helmholtz Centre for Environmental Research – UFZ in
the scope of the SAFIRA II Research Program: Revitalization of Contaminated Land and
Groundwater at Megasites, project “Compartment Transfer”. Further funding was provided
by the Helmholtz Interdisciplinary Graduate School for Environmental Research
(HIGRADE) (Bissinger and Kolditz, 2008).
REFERENCES Bissinger, V. and Kolditz, O. (2008) Helmholtz Interdisciplinary Graduate School for Environmental Research
(HIGRADE). Gaia-Ecological Perspectives for Science and Society, 17, 71-73.
Kappelmeyer, U., Wießner, A., Kuschk, P. and Kaestner, M. (2002) Operation of a Universal Test Unit for
Planted Soil Filters - Planted Fixed Bed Reactor. Eng. Life Sci., 2, 311-315.
Puig-Grajales, L., Tan, N. G., van der Zee, F., Razo-Flores, E. and Field, J. A. (2000) Anaerobic
biodegradability of alkylphenols and fuel oxygenates in the presence of alternative electron acceptors. Applied
microbiology and biotechnology, 54, 692 - 697.
Thomas, A. O. and Lester, J. N. (1993) THE MICROBIAL REMEDIATION OF FORMER GASWORKS
SITES - A REVIEW. Environmental Technology, 14, 1-24.
Wiessner, A., Kappelmeyer, U., Kuschk, P. and Kastner, M. (2005) Influence of the redox condition dynamics
on the removal efficiency of a laboratory-scale constructed wetland. Water Res, 39, 248-256.
Winter, M. and Kickuth, R. (1989) Elimination of sulphur compounds from wastewater by the root zone process
- II. mode of formation of sulphur deposits.