water characteristics

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PHYSICAL, CHEMICAL AND MICROBIOLOGICAL WATER QUALITY

OF THE MANYAS LAKE, TURKEY

AYSEL KARAFISTAN∗ and FATMA ARIK-COLAKOGLUCanakkale Onsekiz Mart University, SUF, Department of Fisheries, 17100 Canakkale, Turkey

(∗ Author for correspondence: Tel.: + 90-286-2180018 Ext. 1684; Fax: + 90-286-2180543;

E-mail: [email protected])

(Received 7 May 2003; accepted in final form 11 December 2003)

Abstract. Manyas, also known as the Bird Paradise Lake, is situated near the south-eastern coastsof the Marmara Sea in Turkey. This shallow lake, is a unique natural reserve providing habitat formigratory birds with its rich fauna and plankton species. The objective of this work is to study theecological and water quality changes resulting from increasing anthropogenic pollution and human

intervention on the natural variations of the water level. For this purpose, physical, chemical andmicrobiological aspects of the aquatic ecosystem in the lake of Manyas are being measured semi-monthly since more than a year. After the completion of field measurements associations betweendifferent parameters will be searched by means of a water quality model. Results obtained willbe used in the sustainable restoration of the lake. In this paper, firstly the nutrient and trophicdynamics of the planktonic ecosystem are associated with the bio-geochemical water cycle in thelake. Secondly, space and time distributions of all physical, chemical and microbiological data arepresented and interactions between the nutrient availability and some microscopic communities arediscussed.

Keywords: chemical and microbiological water quality, indicators, Manyas Lake, nutrient cycles,physical

1. Introduction

Manyas or ‘ Bird Lake’ (40◦11 N, 27◦58 E), is situated 14 km from the south-eastern coasts of the Sea of Marmara, Turkey. Its origin is tectonic, related to thewell known seismicity of the Western Anatolian Fault (Leroy et al. 2002). Manyasis a shallow eutrophic lake with many interesting properties. It receives fresh waterfrom several streams and underground as well. The lake water is always turbid,because of its colloidal and clay content. Water level fluctuates naturally withseasons, reaching the highest level of 6m in spring and the lowest level varyingbetween 1–2 m in summer.

Prof. C. Kosswig was the first to discover in 1938 that the lake lies on an im-portant world wide migratory water bird route. The lake is rich in deep fauna andplankton. There is also considerable amount of birds’ fertilizers. All these factorscontribute to diverse and intensive fish and bird populations, to sustain their lives.The north-eastern part, covering 64 ha consists of woods where more than 266bird species have been recorded to nest and more than 90 to breed. This area is

C Springer 2005Mitigation and Adaptation Strategies for Global Change (2005) 10: 127–143



AYSEL KARAFISTAN AND FATMA ARIK-COLAKOGLU

Figure 1. Localization of the sampling stations at Lake Manyas.

protected since 1959 as the first natural reserve area of Turkey. In 1976 the site wasgranted a class A Diploma by the Council of Europe, recognizing the wetland to

be under protection as habitat for birds and also as a natural reserve. This specialstatus has subsequently been renewed four times (most recently in 1996). Alsoin 1977 the entire lake was declared as a Permanent Wildlife Reserve, under theprotection of the Cultural and Natural Assets Law. In 1994 the eastern part of thelake, covering 10,200 ha, was listed in the Ramsar Convention, with the same statusbeing extended to the whole lake in 1998. The site is managed by the Ministriesof Environment, Forest, Culture, Energy and Natural Resources. The park consistsof partially flooded forests which are mainly meadows and willows. There is anobservation tower and a visitors centre in the park.

Thus, Lake Manyas has been known to be one of the most important worldwide natural reserve for migratory birds and wild fowl species. The site holdssignificant breeding populations of herons (e.g. Night Heron, and Grey Heron).The lake is also an important reproduction area for the Dalmatian Pelican, as wellas Spoonbill and the Pygmy Cormorant liable to global extinction. Large numbersof other cormorants (about 2000 pairs), White Pelican, White Stork, Red-footedFalcon, geese, swans, ducks, terns and pink flamencos are passage birds observedin the area. Oxyura leucocephala has been regularly recorded in winter. The site,

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QUALITY OF THE MANYAS LAKE

since its discovery as a bird sanctuary, is called Kus Cenneti which means ‘ Bird

Paradise’. The lake was once used to support 23 fish species, as well as crayfish,salamanders, turtles, water snakes and frogs. Further Kus Gölü (Figure 1) is import-ant for commercial fishery, mainly Cyprinus carpio. According to archaeologistsand historians (Bakir 1997) in the ancient history of Greece Xenophon describesthe lake as a very large wetland and associates Manyas to ‘Paradise’ 4th centuryB.C. (Leroy et al. 2002).

Around the lake, there are reed, rush and meadow areas. The main vegetationseems to be at the limit of Mediterranean type with white willow as the mostcommon tree. The south and south-west shores of the lake are embanked andthe outflow is controlled by two regulators. During the summer months, when thewater level drops, the area becomes covered in lush vegetation. Some forests in thesouthern part have given place to agricultural areas, lately. There are 14 villagesaround the lake, with agriculture as main activity. Cattle and poultry farming arealso important sources of income. Ten villages discharge solid and liquid wastes

directly to the lake with no purification. Remaining 7 villages have biologicalpurification plants. Also among the 33 neighbouring factories only two possespurification facilities. According to the environmental protection unit of the mu-nicipality, there exists totally 111 polluting point sources (poultry) dischargingdirectly to the streams with only 11 in possession of biological purification means.In addition, runoff from households and numerous farms are being carried directlyinto the lake with no treatment. Intensive use of fertilizers in the nearby farmlandsare also being carried to the lake. In the north-eastern part, Sıgırcı Stream bringschemical pollution from the nearby industrial city of Bandirma. Especially Boronand other chemicals are being processed in these factories.

Runoff from numerous farms, animal processing plants, households and factor-

ies are being carried to the lake directly where current waste treatment facilitieshave insufficient capacity. Under these conditions ‘eutrophication’ is inevitable.This is a well known consequence of nutrient (i.e. nitrate, phosphate and silicate)enrichment of closed or semi-closed water bodies or seas, such as the Mediter-ranean (Karafistan et al. 1998 and 2002).

We know that untreated polluting sources of surface water are responsible forwaterborne bacterial diseases (e.g. cholera and typhoid). On the other hand, thelake receives at all times and by natural means bacteria from soil, air and riversas well as dead plants and organic matter. Only a small amount of these bacteriafind favourable existence conditions and they usually constitute the natural flora of water. We must also add to the natural micro flora the by-products of anthropogenicactivities present in sewage, organic matter wastes from animal plants (especially

poultry in that area) and factories. Microbiological, and hence hygienic, waterquality can be determined from the biologically degradable organic matter (OM).Behaviour of the bacterial loop with respect to nutrients is more complex, however.

Our aim in this work was to determine interactions between the above differ-ent components of the aquatic ecosystem in Lake Manyas. These interactions are

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influenced by both the physical, chemical and microbiological water quality of thelake as described in the following sections.

2. Characteristics of Data

2.1. STUDY AREA

Fluctuations in the lacustrine properties of Lake Manyas, are quite interesting onthe geological scale as a tectonic place, as well as the seasonal one as a naturalreserve. In this work we have limited our analysis to the seasonal variability of certain water quality indicators and parameters. The five sampling stations shownin Figure 1 were selected in such a way to provide a good local representationof each section. Sampling always started at Station 1 and the same trajectory wasfollowed on a fishing boat to the last Station 5. Special care was taken for not

disturbing birds nesting at the national park, located in the vicinity of Station 2.The surveys were done semi-monthly usually, except for February 2003 which wastoo cold for any measurement on the lake.

2.2. WATER QUALITY INDICATORS

Physical, chemical and microbiological water quality indicators were selected withrespect to the following properties;

Physical: The physical water quality parameters that were considered in themonitoring program were temperature, PH, Secchi transparency and depth. Tem-perature is indeed a fundamental factor for water quality, exerting a great influenceover the aquatic system. Factors such as reductions in water flow and waste dis-

charges may have a negative affect on its natural seasonal variability. pH is a knownstandard measure of acidity and alkalinity. It drives many chemical reactions inliving organisms, where a pH value of 7 represents a neutral condition. Theseparameters were measured in situ together with depth and transparency.

Nutrients and Chemical parameters: Nutrients most responsible for water qual-ity degradation via eutrophication are nitrogen, phosphorus and silica. They arefound in the aquatic environment as dissolved inorganic or organic forms. Sincephosphate (PO4), silica (SiO2) and nitrate (NO3) are the most limiting factors forthe phytoplankton growth, they are also considered as water quality indicators.Another nutrient required for life, is the ammonia (NH3) molecule, which can behighly toxic for the aquatic life above a certain concentration. It was thereforeincluded in the analysis. Besides nutrients, metals such as zinc (Zn), iron (Fe),calcium (Ca), magnesium (Mg), silica (Si), copper (Cu) and manganese (Mn) maynaturally be present in the lake water, due to its tectonic origin. Their concentra-tions might as well be modified by anthropogenic activities. Specially Boron (B)processing is the most important activity in that area. It was added to the above listwith nickel (Ni) as chemical indicators of water quality.

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Biological parameters: They consisted of phytoplankton counted per liter, forthe most dominant species relevant to the lacustrine ecosystem. The phytoplanktonwas divided into two groups with different nutritive needs: on the one hand Bacil-

lariophyceae, large diatoms consuming silicate for their growth. Secondly, a groupcomprising several smaller species such as Cyanophyceae, Chlorophyceae whichneed phosphate or nitrate for their growth.

Microbiological: Certain bacteria enter waters through inadequately treatedsewage or runoff of OM from pastoral farm lands. Wild life living in and aroundthe lake are also an important contribution to the production of OM. It is wellknown that bacteria and fungi are responsible for the degradation of OM, and forthis reason they are commonly used as microbiological indicators of water quality.Faecal material is an indirect source of decomposed organic matter (DOM) as thesolids are solubilized during microbial degradation. In fact heterotrophic bacteriaare known to assimilate dissolved OM and N compounds, as ammonium necessaryfor protein synthesis (Lacroix and Gregoire 2002). For this reason, some of these

bacteria are used as water quality indicators when there is not enough nitrogen inthe aquatic environment. Recognized bacterial indicators for assessing water qual-ity are bacteria of the Enterobacteriaceae family defined as total coliform bacteriaand the Fecal coliform bacteria. The coliform bacteria are gram-negative rods, withthe faecal coliform bacteria usually, but not always, found in the faeces of warmblooded animals: The presence of faecal coliform bacteria in water is indicative of contamination by faecal material and considered indicative of health risk. Signi-ficance of coliform group density is established as an indication of the degree of pollution and the sanitary quality of water. Recently, the use of Escherichia coli

suggested as most sensitive indicator of faecal pollution. In addition to the abovebacteria Enterococcus and Staphylococcus are also used as indicators of either

faecal or organic pollution. Other types of bacteria are Pseudomonas; known todegrade nitrogen compounds. Lactobacillus are associated to carbon products andfungi to organic matter. All these bacteria have also been included in the analysis asindicators of water quality, even though the results are not presented in this work.Especially Enterococcus and Staphylococcus are important indicators of the wholeaquatic ecosystem health, including fish and birds via the food web. Indeed both

Escherichia coli and Enterococci are good indicators of gastrointestinal diseases.The presence of such bacteria indicates the possible presence of faecal material.Therefore, indicator bacteria concentrations are also used to determine if the waterquality is adequate for recreation. They are sometimes combined with the Pseudo-

monas bacteria which are well associated with skin infections. For this reason, weused Pseudomonas and enter bacteria as indicators of microbiological water quality

in this lake.

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3. Method of Analysis

Physical parameters were measured directly at the water surface by conventional

methods (Wetzel and Likens 1995). Two liters of water was collected by a watersampling bottle (Ninsin) at each station and carried to the laboratory (200 km)away. Standard photometric (Palintest 7000) analysis was employed for chemicalconcentration determinations. Nutrient concentration measurements were calib-rated and found to be competitive with those obtained by the autoanalyzertechnique of the Institute of Marine Science, at Erdemli. For the microbiologicalsampling, two replicate water samples were taken 10 cm below the surface, andcollected in 150 ml glass sample containers. Water samples were brought to thelaboratory in ice boxes and analysed within 24 hours.

Indicator bacteria were measured as a concentration, usually expressed as anestimate of the number of individual organisms per ml of water. Water qualitymanagers are interested in both the concentration of single samples, and in the ‘av-

erage’ concentration of a series of samples taken over a period of time (Baumgart1993; Schulze 1996). Evaluation of heterotrophic bacteria was done by plating onhighly selective culture media. In our microbiological laboratory, 7 different typesof commercial Agar plates given in Table I, were used. Incubation conditions andmethod used for each culture are explained in the references. Colonies formedafter the necessary incubation period were counted directly, and the logarithm of the arithmetic means were used in the graphical presentations.

3.1. SPACE AND TIME DISTRIBUTIONS OF WATER QUALITY PARAMETERS

Annual variations of the 4 physical parameters are given in Figures 2 (a–d). Distri-

butions of phytoplankton associated with the nutrients are shown in Figures 3, 4.In these figures we observe that the degree to which the phytoplankton growth islimited by the nutrient availability is variable with respect to the local conditions.Microbiological test results are presented through the Figures 5 to 6. They are alsocompared with the availability of the nitrogenous products such as ammonium,nitrate and nitrite. As expected heterotrophic activity of Pseudomonas and enterbacteria, continue in winter when ammonium is at the highest level. In Figures7 and 8 space and time variability of some chemical parameters are presented.The last figures reveal that the instantaneous peaks observed in December, shouldobviously be due to discharge from point sources. From these figures one easilynotices that, besides the natural variability, the water quality and attributes of thissite are fluctuating rapidly both in space and time.

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TABLE I

Incubation conditions and nutritive plates used analysis of microorganisms in LakeManyas.

Plate Micro organism Incubation

days T(◦C)

PC Total aerobic bacteria 3 30

(Plate Count Agar)

VRBG Enterobacteria 1 30 (anaerobe)

(Crystal Violet Galle Glucose Agar)

GSP Pseudomonas 3 22

(Pseudomonas-Aeromonas Agar)

BP Staphylococcus 3 37

(Baird Parker Agar)

MRS Lactobacillus 3–5 30 (anaerobe)

(M.R.S. – Agar, pH-5)

KA Enterococcus 3 37

(Kanamycin Agar)

MALZ Fungi 5 22

(Malt Extract Agar)

4. Results and Discussion

The annual mean surface water temperature of Lake Manyas is around 12.5 ◦

Cin accordance with the meteorological mean (Figure 2a). The highest temperatureof 25 ◦C is reached in July-August, and the lowest value of 2 ◦C was recorded inDecember.

pH > 7 in Figure 2b indicates alkaline conditions in the lake, which is quitevariable throughout the seasons. It reaches maximum values of 8–9.5 at someplaces in June-July, and similar to temperature has its minimum in December atall stations. We know that some biological processes may adversely be affected bysudden pH changes, which in return deteriorates the whole water chemistry. FromFigure 2c we also notice that, even though the lake water is usually turbid, theSecchi transparency reaches 1.75 meters in May at the central station, where totaldepth is around 4 meters (Figure 2d).

Distributions of the most abundant diatom ( Bacillariophyceae) are shown inFigure 3. Two bloom periods are occurring in June–July and in December, withabout the same intensity. As expected, the maximal diatom concentrations aredirectly followed by the minima of silicate. Similarly, we observe in Figure 4the seasonal distributions of the smaller surface phytoplankton populations as a

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Figure 2. Seasonal distributions of physical parameters; a) pH, b) Temperature, c) Secchi depth, d)Depth.

function of nitrate or phosphate as growth limiting factors. Chlorophyceae seemto have a major peak in the north-western Station 1, in May. The bloom periodfor the same phytoplankton have shifted to June for the north-eastern Station 2(Bird Paradise), where the maxima correspond directly to the minima of NO3. Asecondary PO4 peak follows in winter, especially at Station 1. This may be due tothe fact that no small phytoplankton seem to be present at that time of the year. The

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Figure 3. Distributions of diatom and silicate; a) Bacillariophyceae, b) SiO2 in Lake Manyas.

same type of correlation is observed for Cyanophyceae, mostly abundant at Station

1 in May, with a corresponding NO3 decline in June.Pseudomonas bacteria are known to assimilate directly the nitrogen present inammonia. This is easily noticed in Figure 5 where a rapid decrease in Pseudomonas

bacteria in April 2003 is followed by an abruptly increasing peak in ammonia,in May 2003. As shown in Figures 6, heterotrophic activity of some (e.g. enterbacteria) are similar in behaviour, accept the central Station 3 where enter bacteriaconcentrations in August are above the bathing limit of EU-regulations (EU 1995).Again the decrease in ammonium concentrations follow the bacterial peaks ratherrapidly. On the other hand, exceedingly high concentrations of ammonia occurringin spring at Station 5 should be due to the nearby organic poultry pollution which isbrought by streams. Nitrite concentrations are showing low fluctuations throughoutthe year, and a direct correlation is difficult to establish at a first glance. Sulph-ate, which is also associated to the bacterial activities is very high in December(Figure 8a). It seems also plausible that the microbial regeneration of N occursthroughout the year and in winter it reaches its highest level.

Indeed, for drinking water no faecal coliform should be present and they are notwanted in general in the marine and lacustrine waters used for various purposes

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Figure 4. Small phytoplankton and nutrient dynamics; a) Chlorophyceae, b) Cyanophyceae, c) NO3,d) PO4.

(bathing, fishing, etc.). However, from the Figures 5 and 6, representing the mostabundant indicator bacteria, we observe a significant continuous presence. Accord-ing to general water pollution regulations, water quality in all stations is of classIII or even IV at the Natural Park. Compared to the EU microbiological water

quality criteria (EU 1995), the Park receiving pollutants from the Sıgırcı Stream

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Figure 5. Pseudomonas bacteria and nutrient distributions; a) Bacterial counts, b) NH3, c) NO2.

has the highest number of Fecal and total coliform bacteria. This is a confirmationfor class IV, as an extreme level of pollution in this site, serving as habitat to birds.We intend to extend the microbiological water quality analysis to micro flora of fish in the future, in order to establish the level of pollution at the last chain of thefood web.

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Figure 6. Distributions of Enterobacteria and nutrients; a) Bacterial counts, b) NH3, c) NO2 in LakeManyas.

Distributions of Ca, Mg, Fe, Ni concentrations are presented in Figures 7a to7d. Those of SO4, B, Cu, Zn follow in the last Figure 8. Accept for Ca and Mg,which are naturally present in water (particularly at Station 4 with springs) abruptincreases in the concentrations of Fe, Ni (Figures 7c, 7d) and that of SO 4, B, Cu,Zn (Figures 8a–8d) are encountered in December 2002, at Stations 1 and 5. Onthe other hand, in Stations 1, 5, 3 Ca increases (Figure 7a) in May 2002, and thatof Mg in March 2003 (Figure 7b) are observed. The fact that concentrations of

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Figure 7. Distributions of parameters; a) Ca, b) Mg, c) Fe, d) Ni in Lake Manyas.

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Figure 8. Distributions of parameters; a) SO4, b) B, c) Cu, d) Zn in Lake Manyas.

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these elements show such instantaneous peaks, at Stations 1, 5, must be due todischarge from numerous surrounding factories without purification. For example,one of the largest borax and boric acid production industries in that region ( Etibor )has been estimated to discharge wastes about 6300 m3 /day. Sıgırcı Stream, itself,is probably feeding the Park with 1700 m3 d−1 of B products it is receiving fromthis factory. From Figure 8b boron is seen to have two principal peaks, one in May2002 and another the following December. Boron is also known to be limiting plantgrowth and the degree of B pollution may create serious problems for the trees andvegetation in that area.

5. Conclusions

It is, indeed difficult to judge about the degree of long term pollution and waterquality from short period measurements. The results presented in this work are

based only on observational analysis of one year measurements. It is evident evenfrom this picture alone that, Lake Manyas is facing many adverse factors in termsof the quality and quantity of water it is receiving. The lakes’ water which waspotable in 1960s, has been observed to deteriorate in quality very rapidly the lastdecades by many researchers, because of the anthropogenic activities. Also due toover fishing, and the artificial water regime, fish and bird populations have beendeclining considerably the last years. It is well known that natural water levelfluctuations are vital for the aquatic ecosystem health from the microscopic tothe macroscopic trophic level, since all are related by the aquatic food chain. Itseems, however, that the water level has been kept relatively high in recent yearsfor making use of the lake as a reservoir for irrigation. The forest not being subject

to any management scheme neither, feeding marshes and nesting trees for birds arelost in some areas due to prolonged inundation.In this study, it was demonstrated that Lake Manyas as a natural reserve, is

threatened by all types of anthropogenic pollution which have the impact and po-tential to alter the productivity of the whole ecosystem, via the food chain. Thus,any perturbation in the chain may also alter the water quality besides the quantity.As an example, nutrients such as N, P, and Si, which are most often responsiblefor water quality degradation and eutrophication were considered. Their seasonalvariability were studied at 5 selected important spots. As a consequence, it wasfound that the degree to which the phytoplankton growth is limited by this nutrientload alone, depends on the local conditions and also varies with its availabilityon the seasonal scale. Certain diatoms were observed to be abundant with twobloom periods which corresponded to silicate minima. For the smaller phytoplank-ton species, a late spring or early summer bloom corresponds with a phase lagto a nitrate minimum. The latter is followed by a phosphate maximum, whichis in good accordance with the fact that phosphate is the growth limiting factorin that case. Hence the phytoplankton consume first the most available nutrient,

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which is nitrate in our case. Indeed, other growth-limiting factors such as light,temperature as well as grazing pressure from zooplankton are also important forphytoplankton. All data are not yet completely analysed at this stage and in orderto understand the nutrient cycling through the eutrophic lake ecosystem, long termfield measurements are required (Karafistan et al. 1998). When all measurementsare synthesized, rates and fluxes of nutrients transported through each compartmentwill be estimated. These data will then be used as input in a one-dimensional (1-D) physico-chemical water quality model in order to predict the feature behaviourrelevant to this lacustrine ecosystem. Model will be 1-D, since the water is con-sidered to be completely mixed and each station seems to have completely differentcharacteristics depending on the polluting sources. In sedimentation basins such asLake Manyas, retention of nutrients is also possible. Residence time of water andrenewal characteristics will be taken into account in the study of dispersion of pollution. The final results will help in monitoring, conservation and restorationmeasures to be taken.

Besides the conventional physical and bio-geochemical water quality proper-ties, the microbiological ones were also our particular concern for Lake Manyasas a natural reserve. We have demonstrated that the heterotrophic activity of somenitrogen fixing indicator bacteria continue even in winter. This should be due tofavourable conditions such as the availability of nitrogenous products. It was alsonoticed that the microbial regeneration of nitrogen occurs throughout the year,reaching its highest level in winter. Sulphate was also found to be high in Decem-ber. These properties will be incorporated to the water quality model mentionedabove. Even though pathogenic sewage organisms do not live long in water, puri-fication is absolutely necessary. From our observations we have also revealed theneed for more measurements and data concerning the previous hydrological re-

gime, geographical, meteorological and topographic parameters, as well as remotesensing observations, surrounding land and water uses.As a sound protection and a first management plan we have recommended to

the Scientific and Technological Research Council of Turkey (TUBITAK) that firstof all the water regime should be returned to its previous natural level. With TU-BITAK’s intervention we have lately established contact with authorities in thatarea. Our first hand results will be presented to the directorate of the museumof the natural Park and the council of the municipality. As a management andrestoration plan the most polluting point sources will be urged for cooperationin a sustainable purification program. Help from the gendarmerie will be askedfor control and surveillance. Other public authorities will also be notified on theconsequences of pollution in the lake. All purification plants should be operational.

To our knowledge the lake will be loaned for 4 years to the fishing cooperative of Lake Manyas. Inconveniences of over fishing will be explained to the fishermen of that area. School children will be educated on water quality and bathing conditions.According to the latest good news, as a measure against B pollution, a reservoir for

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collecting boric and other discharges in that area has been constructed recently andit will soon be operational.

The results obtained thus far were also presented at the International ZoologyConference (October 23–25, 2003 Istanbul) dedicated to the 100th anniversary of C. Kosswig.

Acknowledgements

Field work and laboratory analysis were funded by the Scientific and TechnologicalResearch Council of Turkey, (TUBITAK, with project grant YDABAG 101Y118).This work has also been realized with technical and financial support from theResearch Foundation of the Canakkale Onsekiz Mart University. We are grateful toResearch assistants S. Sagir, F. Cakir and D. Odabasi, the Museum of National Parkat Kus Cenneti, together with the Fisheries Union of Bereketli Village in Manyas,

environment protection (gendarmerie) unit of the municipality of Bandirma fortheir kind help and information provided about the field area.

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