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A survey to determine levels of chlorinated pesticides and PCBsin mussels and seawater from the Mid-Black Sea Coast of Turkey
Perihan Binnur Kurt a,*, Hulya Boke Ozkoc b
a Department of Environmental Engineering, Faculty of Engineering, Akdeniz University, 07200 Topcular, Antalya, Turkeyb Department of Environmental Engineering, Faculty of Engineering, Ondokuz Mayis University, 55139 Kurupelit, Samsun, Turkey
Abstract
A mussel and seawater monitoring survey was conducted at six sampling points between Yalikoy (Ordu) and Sinop in 1999–2000along the Mid-Black Sea Coast of Turkey in order to assess concentrations of organochlorine pesticides (OCs) and polychlorinated
biphenyls (PCBs). Chlorinated pesticides and PCBs were measured in the mussel Mytilus Galloprovincialis and in seawater. In the
mussel samples, the most common pollutants in terms of average concentration per g of wet weight (ww), were DDT (max. 1800 pg/
g ww, min. 240 pg/g ww) and its metabolites DDD (max. 5400 pg/gww, min. 240 pg/g ww) and DDE (max. 2800 pg/g ww, min. 70
pg/g ww). Also, dieldrin, heptachlor and HCB were notable contaminants in the mussel samples. PCBs were determined in none of
the biota or seawater samples. The concentrations of the OCs and PCBs in mussels were higher in coastal areas receiving river
discharges and close to the largest city of the region, Samsun (especially in sampling points in the harbour area). The well-known
long persistence of DDTs and other chlorinated compounds was confirmed by residues of these pollutants measured in mussels. On
the other hand, even though the usage of such kind of persistent compounds in Turkey was banned, there may still be illegal usage
and it is not certain whether the application of these compounds did end in the region.
Ó 2003 Elsevier Ltd. All rights reserved.
Keywords: Black Sea; Turkey; Mytilus Galloprovincialis; Monitoring; OCs; PCBs
1. Introduction
There is widespread concern about chemical pollu-
tion reflecting increasing population, agricultural activ-
ities and industrial development (Travis and Hester,
1991), and the coastal environment is particularly at risk
from the effects of these contaminants (Wade et al.,
1998). Organisms that live in aquatic environments are
suitable representative samples for assessing pollution
and mussels are used in many pollution monitoring andassessment studies because: they have world-wide geo-
graphical distributions; they are relatively stationary
reflecting contamination better than mobile species; they
can concentrate the chemicals 102 –105 times higher than
the water they live in (Farrington et al., 1983; Villeneuve
et al., 1999) by uptake as they can filter large volumes of
water (Kryger and Riisgard, 1998) and remove all seston
(suspended particles) between 1 and 250 l (Jorgensen
et al., 1984); they have little ability to degrade most
chemicals due to lack of necessary enzymes; and they are
important for public health due to being prefered food
for many people (Farrington et al., 1983; Villeneuve
et al., 1999).
The mussel Mytilus galloprovincialis, is common
along the Black Sea Coast of Turkey due to the low seawater temperature and salinity which are the optimum
conditions for life and productivity of M. galloprovin-
cialis (Uysal, 1970).
The marine environment of the Black Sea Coast of
Turkey has degraded recently due to increased usage of
the region, and it has been impossible to estimate the
pollution loading in this agricultural and industrial
coastal area (Tufekci, 1996). In the past two decades, the
Black Sea has been threatened with problems from chlo-
rinated compounds as well as other chemical pollutants
(Bakan and Buyukgungor, 2000; Tuncer et al., 1998).
* Corresponding author. Tel.: +44-1524-592578; fax: +44-1524-
593985 (till July 2005), tel.: +90-242-323-23-64; fax: +90-242-323-23-
62 (after July 2005).
E-mail addresses: [email protected], perihankurt@akdeniz.
edu.tr (P.B. Kurt).
0025-326X/$ - see front matter Ó 2003 Elsevier Ltd. All rights reserved.
doi:10.1016/j.marpolbul.2003.12.013
www.elsevier.com/locate/marpolbul
Marine Pollution Bulletin 48 (2004) 1076–1083
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Transport of various pollutants by many rivers and
streams passing from the main agricultural and urban
areas of Turkey and other neighbouring countries is the
main source of pollution in the Black Sea. From Tur-
key’s side, Kizilirmak and Yesilirmak are probably the
main rivers in this pollutant transport, and both of these
rivers reach the Black Sea in this study area (Pinarli
et al., 1991; Bakan et al., 1996; Bakan and Buyukgun-
gor, 2000; Tuncer et al., 1998). Carsamba and Bafra
Basins are the two main agricultural basins of Turkey in
the region and these rivers receive many pollutants
including pesticides from these basins as well as from the
cities which they pass through (Bakan et al., 1996;
Tufekci, 1996; Ozkoc et al., 1999; Tuncer et al., 1998).
Additionally, due to lack of proper sewage and waste-
water treatment systems in most cities in the region,
wastewater from these cities has been discharged directly
either to these two main rivers or to smaller other rivers
or directly to the Black Sea (Pinarli et al., 1991; Bakan
et al., 1996; Tufekci, 1996; Tuncer et al., 1998).Due to high annual rainfall in the region, floods result
in transport of contaminants from agricultural areas to
the sea. Also, due to a high population increase in the
region, land-filling along the coast is common, and thus
another pollution transport pathway is being created.
Important also are atmospheric deposition, global dis-
tribution and transportation of chlorinated compounds
as well as their persistence and long life cycles, which
increase the occurrence of these pollutants in the region
(Ozkoc et al., 1999).
Because of their environmental persistence, accumu-
lation capacity and toxicity, there is increasing globalconcerns for chlorinated compounds in the environment
and these concerns have led to the gradual reduction of
these compounds all over the world. Production of DDT
was reduced in 1960s and after recognition of its envi-
ronmental hazards, its use was banned in the 1970s in
economically developed countries (e.g. it was banned in
France in 1975) but it is still being used in many
developing countries (especially in African countries).
PCB production was reduced slowly in the 1970s in most
European countries but PCBs still remain a potential
threat (Phillips, 1986; Kruus, 1991; Villeneuve et al.,
1999). Although production and usage of many chlori-
nated compounds such as Dieldrin, Aldrin, Endrin,
Chlordane, DDT, BHC, Lindane and Heptachlor were
completely banned in Turkey in the 1990s, total pesti-
cide usage in Turkey in 1995 was 37,000 tons, and this
usage shows a steady increase year by year (TCV, 1998).
Although there are some studies related to organo-
chlorine compounds in the region, data from these
studies either concerned mussels from a different part of
the region (Telli, 1991) or from main rivers as annual
fluxes (Tuncer et al., 1998). Therefore, this study isimportant as the beginning of a series of surveys based
on the ‘‘mussel watch’’ concept, and will serve as a guide
for future surveys to monitor trends of pollution risk
from chlorinated compounds in the Mid-Black Sea
Coast of Turkey (Ozkoc et al., 1999).
2. Materials and methods
2.1. Sampling
Fig. 1 shows the the sampling points which were lo-cated along the Mid-Black Sea Coast of Turkey, from
Yalikoy (Ordu) to Sinop. Mussel and sea water samples
Fig. 1. Study area and location of sampling points.
P.B. Kurt, H.B. Ozkoc / Marine Pollution Bulletin 48 (2004) 1076–1083 1077
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were collected three times from six sampling points in
1999 and 2000. Composite samples were collected from
Sinop and Yalikoy (Ordu) due to an estimated low pol-
lution risk for these contaminants; therefore only one
sampling point was conducted in these places. The major
study area was the Samsun coast where four sampling
points were chosen. Sampling point selections were based
on proximity of industrial facilities, sewage discharge and
distance from river deltas. One sampling point selected
was very close to the Mert River in Samsun, which is the
most polluted river passing through the city. Two sam-
pling points were in the harbor area and the last one was
very close to a landfill site. Sea water sampling was car-
ried out at the same sampling points. Due to fast urban/
industrial development along the coastal area, mussel
populations no longer exists at several points on the coast
of the region, and the occurrence of mussel populations
was of course an important factor in determining sam-
pling points and sampling times.
A large number of mussels of similar size (4–8 cmshell length) were collected from each sampling point.
These mussel samples were stored in pre-cleaned alu-
minium coated containers and transported to the labo-
ratory as soon as possible after collection. In the
laboratory, after measuring the width, length and weight
(with shell) of each mussel, the mussels were opened
with pre-cleaned stainless steel knives; the soft parts
were removed and frozen for analysis. The sampling
procedure could only be repeated three times in the year
because suitably sized mussel samples could not be
found. The samples were homogenized and 20 g of
samples were analysed for OCs and PCBs followingwell-established standard techniques of UNEP, IAEA
and FAO (UNEP/IOC/IAEA, 1988, 1995, 1996; UNEP/
FAO/IAEA/IOC, 1991; IOC, 1993).
3. Determination of chlorinated pesticides and PCBs in
mussel and water samples
3.1. Mussel samples
After homogenization of the mussel samples, pre-
cleaned anhydrous sodium sulphate was used to removethe water content of the samples. Before the extraction
of samples, a pre-extraction procedure was applied to
glassware, cellulose extraction thimbles and sodium
sulphate using a Soxhlet apparatus. Twenty grams of
homogenized mussel samples were mixed with anhy-
drous sodium sulphate, and then extracted in a Soxhlet
apparatus for 8 h using 250 ml of glass distilled 1:1
DCM:hexane mixture. In order to calculate recoveries,
all samples were spiked with 25 ng/ml of 2,4,5 TCB
(trichlorobiphenyl) and e-HCH as internal standards.
An extracted aliquot of 10 ml was also removed for lipid
content analysis. DCM:hexane extracts were concen-
trated to about 15 ml using a rotary evaporator and they
were evaporated to a few milliliters in a water bath
(about 70 °C). An aliquot of this extract was taken for
treatment with concentrated sulphuric acid to destroy
lipids. Both aliquots were through the florisil clean-up.
Analytes were back extracted with 60 ml of hexane. This
extract was evaporated to 1 ml in a water bath and then
cleaned-up using florisil chromatography column to
separate classes of compounds in different fractions as
described below.
Activated florisil (at 130 °C for 12 h) was used to pack
a clean-up column. From the florisil column, the first
fraction was obtained by eluting the sample with 70 ml
of hexane, this fraction contained mainly PCBs, HCB,
DDE and Aldrin. The second fraction was obtained
with 50 ml of a freshly prepared mixture of 70:30 hex-
ane:DCM and it contained toxaphene, DDD, DDT,
HCH. The third fraction containing Endrin and Diel-
drin was eluted with 40 ml of DCM and this fractionwas recovered only from the aliquot of the sample ex-
tract not treated with concentrated sulphuric acid, since
H2SO4 destroys Dieldrin and Endrin. Forty milliliter of
hexane was added to the evaporation flask of the third
fraction directly for solvent exchange. A blank sample
was prepared using 30 g of pre-cleaned sodium sulphate
to determine any contamination during analyses and the
same procedures were applied to the blank sample as
to mussel samples.
All fractions were further concentrated to about 1 ml
and analyzed by gas chromatography (Fisons HRGC
Mega 2 Series) equipped with an electron capturedetector (ECD 800) and a capillary column (DB-5, 30 m
long, 0.32 mm id, coated with 0.245 lm film). The
injector temperature was 250 °C, the detector at 300 °C
and the oven programmed from 70 °C for 2 min up to
260 °C with a range of 3 °C per min. The carrier gas was
nitrogen with a flow of 2 ml/min and the make-up gas
was helium with a flow of 20 ml/min. Added standards
included a-, b-, c- and d-BHC, Heptachlor, Aldrin,
Heptachlor Epoxide, Endosulphane-I, Endosulphane-
II, Endosulphane Sulphate, Endrin, Endrin Aldehite,
Dieldrin, Lindane, HCB, pp 0-DDE, pp
0-DDD, pp 0-DDT,
Arochlor 1260 and Arochlor 1254.
3.2. Water samples
In order to recover compounds of interest, a liquid–
liquid extraction process was applied to 1 l of water
sample with a total of 240 ml of hexane in three steps.
Before starting the extraction process, samples were
spiked with 25 ng/ml of internal and recovery standards.
A blank sample was prepared with 240 ml of hexane.
After extraction process, the same clean-up processes as
for mussel samples were applied to water sample ex-
tracts, except H2SO4 treatment.
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3.3. Quality control
Blanks were included at a rate of one for every five
samples and were treated in exactly the same manner as
the samples. Average recoveries of internal standards
ranged from 30% to 99% for mussel samples, while it
ranged from 40% to 85% for seawater samples. All re-
sults are blank and recovery corrected. Detection limit
was based on mean blank plus three times the standard
deviation of replicate blank analyses. Detection limits
were 24 pg/g and 0.2 pg/ml for mussel and seawater
samples respectively.
4. Results and discussion
Average concentrations of chlorinated pesticides and
PCBs in mussel and sea water samples during the study
period are shown in Tables 1 and 2 respectively. Many
chlorinated pesticides were determined in both types of sample but no PCBs were detected in any sample. Lipid
content of mussel samples ranged from 11 to 30 mg/g.
In mussel samples, DDT concentration was quite
high, ranging from 240 to 1800 pg/g ww and these con-
centrations depended on the location of sampling. The
concentrations of DDE and DDD ranged from 70 to
2800 pg/g ww and from 240 to 5400 pg/g ww respec-
tively. At the end of the analysis, it was observed that
DDD and DDE were in higher concentrations than
DDT. This result is similar to results in ICES (1974).
DDE especially occurs in higher organisms as a
metabolic product. Mussels are in the second step of the
food chain in aquatic environment (Alloway and Ayres,
1994), and they obtain their food, mainly plankton, by
filtering large amount of water (Uysal, 1970). Thus this
result is not very surprising and it also suggests the
bioaccumulation of DDT and its conversion to DDD
and DDE in metabolism (Roger and Lea, 1972; Ville-
neuve et al., 1999).
The persistent half-life of DDT in aquatic environ-
ments has been suggested to be approximately 5 years
(Villeneuve et al., 1999) and 10–20 years (estimated from
studies) on bivalves (Sericano et al., 1990). DDT can be
transformed to DDE and DDD slowly in this process
(Klumpp et al., 2002). The prohibition of use of DDT in
Turkey is considered to be the late 1980s, so it is not
surprising to find very high concentrations of DDT in
biota samples. On the other hand, it is thought that
there is still continuous input of this compound into
marine environment from atmospheric deposition of DDT (Villeneuve and Cattini, 1986) and DDT probably
leaches from highly DDT contaminated areas and
agricultural soils as well as illegal usage in the region
and other countries. Additionally, there may be input
from illegal usage of these compounds in the region.
DDE, which is the most often recognized metabolite of
the DDT is a very slowly degradable compound. Al-
though DDD production is completely banned in the
world, it was produced and sold under the name ‘‘Ro-
thane’’ for several years (Washington State Pest. Mon.
Table 1
Average concentrations of chlorinated pesticides and PCBs in mussels from the Mid-Black Sea Coast of Turkey in 1999 and 2000
Compound Baruthane (1),
pg/gwwa
Yesil Fener (2),
pg/gwwa
Kirmizi Fener (3),
pg/g wwa
Belediye Evleri (4),
pg/g wwa
Sinop (5),
pg/g wwa
Yalikoy (6),
pg/g wwa
a-BHC 5 nd 8 600 190 50
b-BHC 12 13 70 3900 22 140
c-BHC 3 18 8 nd nd nd
d-BHC 2 1 200 nd nd 30
p ; p 0-DDT 290 400 240 1800 1100 nd
p ; p 0-DDE 2800 300 70 2400 230 120
p ; p 0-DDD 950 850 2200 1000 240 5400
Dieldrin 780 180 130 600 380 360
Endosulfan-I 4000 nd 600 16,000 80 20
Endosulfan sulphate 5700 nd 790 3400 nd 7Endrin 180 310 180 1500 190 20
Endrin aldehide 1300 140 420 1200 nd 3
Heptachlor 110 20 14 1600 40 8
Heptachlor epoxide nd nd nd nd nd nd
HCB 270 170 nd nd 180 nd
Lindane 130 160 nd nd 120 nd
Aldrin 590 nd 70 nd nd nd
Endosulfan-II 270 2100 nd 11,000 12 2
PCBs nd nd nd nd nd nd
Yesil Fener (2) and Kirmizi Fener (3) sampling points are in harbor along Samsun Coast, Baruthane (1) is on west part of Samsun Coast and
Belediye Evleri (4) is on east part of Samsun Coast.
nd¼Not detected.a Bolded numbers are below detection limit.
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Prog, 1996). Another reason for high concentrations of
DDD and DDE compared to DDT in mussel samples is
the metabolism and discharge of DDT from the body of
mussels rather than DDD and DDE’s (Roger and Lea,
1972; ICES, 1974).
Other compounds determined in mussel samples were
Dieldrin (max. 780 pg/g ww, min. 180 pg/g ww), Hep-tachlor (max. 1600 pg/g ww, min. 40 pg/g ww) and HCB
(max. 270 pg/g ww, min. 170 pg/g ww). In spite of
banning and ending of usage of these compounds in the
early 1980s, some compounds such as Heptachlor and
Chlordane are still being used to fight termites and ants.
Heptachlor is the main constituent of chlordane and it
occurs as a result of the degradation of chlordane. HCB
occurs as a result of degradation of some compounds
such as Lindane and therefore it is not surprising to find
HCB in an environment where Lindane is present. HCB
has also been produced as a by-product and in its own
right (Washington State Pest. Mon. Prog, 1996).
In Table 3, a comparison is given of results with othersimilar survey results for mussels. According to the re-
sults of this study, the concentrations of chlorinated
pesticides in mussels in the Mid-Black Sea Coast of
Turkey are much higher than concentrations in mussels
obtained from similar studies in other parts of the
world. Also, as it is seen from Fig. 2, Human Health
Criteria and Wild Life Criteria of EPA are exceeded in
most of the sampling points for different chlorinated
compounds. Especially, DDT and its metabolites DDE
and DDD andP
BHCs concentrations are noticeably
high compared to other similar surveys (Table 3) and
EPA criteria (Fig. 2A–D respectively) and this confirms
the long life and persistence of these compounds in the
environment and also the observed high concentration
of DDTs can be assigned as a sign of the continuing
illegal usage of DDT in the region as reported by Tuncer
et al. (1998). Although concentrations of Dieldrin and
HCB (Fig. 2E and F respectively) are not as high as theconcentrations of DDT and its metabolites, values are
still higher than EPA criteria. PCB pollution was not
observed in any of the sampling points.
Unfortunately, the kind of survey reported here for
chlorinated compounds has not been carried out previ-
ously in the Mid-Black Sea region for the same sampling
area. Therefore, there is no data to compare these results
with in order to assess the trend of pollution in the re-
gion. Although there are similar surveys reported for
chlorinated compounds, one of these surveys (Telli,
1991) was carried out in mussel and sea water in a dif-
ferent area in the Black Sea and the other study (Tuncer
et al., 1998) was carried out in rivers in the region givingthe annual pollutants fluxes. There is no doubt that it
would be better if the same sampling points were used in
both surveys to get a time trend of these pollutants. But,
the same sampling points as those of Telli (1991) could
not be included in this study due to long distance and
limited budget of the study. Due to lack of a previous
dataset from a survey for the same sampling area, results
could not be compared with each other to determine
past contamination or to estimate a trend.
In water samples, heptachlor was the chlorinated
compound with the highest concentration of max. 30
Table 2
Average concentration of chlorinated pesticides and PCBs in seawater from the Mid-Black Sea Coast of Turkey in 1999 and 2000
Compound Baruthane (1),
pg/mla
Yesil Fener (2),
pg/mla
Kirmizi Fener (3),
pg/mla
Belediye Evleri (4),
pg/mla
Sinop (5),
pg/mla
Yalikoy (6),
pg/mla
a-BHC 0.6 nd 1 nd nd nd
b-BHC 7 nd nd nd nd nd
c-BHC nd 0.3 nd nd nd nd
d-BHC 3 nd nd nd nd nd p ; p
0-DDT nd nd nd nd nd nd
p ; p 0-DDE nd nd nd nd 1 nd
p ; p 0-DDD nd nd nd nd 105 nd
Endosulfan-I nd 0.1 1 15 nd nd
Endosulfan sulphate nd nd nd nd nd nd
Endrin nd nd nd nd nd nd
Endrin aldehide nd 0.5 nd nd 15 nd
Heptachlor 0.7 0.2 30 1 1 1
Heptachlor epoxide nd nd nd nd nd nd
HCB nd nd 8 2 nd nd
Lindane nd nd nd nd nd nd
Aldrin nd nd nd nd nd nd
Endosulfan-II 6 nd nd 2 nd nd
PCBs nd nd nd nd nd nd
Yesil Fener (2) and Kirmizi Fener (3) sampling points are in harbor along Samsun Coast, Baruthane (1) is on west part of Samsun Coast and
Belediye Evleri (4) is on east part of Samsun Coast.
nd¼Not detected.a Bolded numbers are below detection limit.
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pg/ml and min. 0.2 pg/ml. Other compounds were not
found because these compounds are hydrophobic and
tend to accumulate in fatty tissue of organisms and in
sediments. Therefore, concentrations of chlorinated
compounds in water are lower than the concentrations
in organisms and sediments (Alloway and Ayres, 1994).
No PCBs were found in both seawater and mussel
samples.These high concentrations of chlorinated compounds
can be considered to be evidence of heavy contamina-
tion of chlorinated compounds for the region in both
past and present times. Chlorinated pesticides as a cer-
tain class of persistent organic pollutants have long
biochemical half-lives in the environment. For instance,
the biochemical half-life of DDT in the environment is
at least 15 years (Carvalho et al., 1996; EEA, 2002). The
results of the study are not surprising when long half-
lives of these compounds in the environment are
considered. On the other hand, due to continued
atmospheric depositions from remote sources to the
Mediterranean and Black Sea as well as other regions of the world, leaching from heavily chlorinated compounds
used and contaminated agricultural areas, concentra-
tions of these compounds are very high and it can be
concluded from the results that these concentrations will
remain at measurable levels for several years.
In water samples, concentrations of the pollutants
were very low compared to the mussel samples. This
result confirms that these compounds are hydrophobic
and tend to accumulate in fatty tissue of organisms and
also in sediments (Chau and Afghan, 1982; Alloway and
Ayres, 1994; Bioaccumulation, 1997).
The whole Black Sea region receives a very heavy
pollution load and this is increasing over time. While
people are polluting the sea and coastal area in the
region, they also consume fish, mussels and other sea
organisms as food. When the increasing accumulation
potential of these compounds in the food chain is con-
sidered, it is clear that humans are the most affected
organisms in the food chain. Although mussels are notpreferred seafood for Turkish people, the detected level
of contamination can still be a threat for public health
since fish is the most common preferred seafood in the
region. In 1999, the amount of annual mussel (Medi-
terranean mussel) production in the Black Sea region
was 1600 t/a and annual export of mussel of Mytilus
spp. and Perna spp. from the whole country was 0.15
and 10 t/a respectively. As seen from the statistics, total
mussel catch in the region is not as much as other
European countries. However, catch of fish is nearly 300
times of catch of mussel in the region. (Fisheries Sta-
tistics, 1999). When the place of fish in aquatic food
chain is taken into account, it is obvious that this kind of pollution in the region is very important for public
health. Since there was no data on catch of M. gallo-
provincialis in the region, it did not seem very mean-
ingful to calculate the tolerable daily intake (TDI) value
using these statistics and to correlate the results with
public health.
Because of important environmental and human
health based reasons, more coastal water and marine
organisms watch programs (i.e. mussel watch programs)
must be carried out comprising the whole Black Sea
Coast of Turkey as well as other countries of the Black
Table 3
Comparison of study results with similar study results from different geographical locations
Study area p ; p 0-DDT,
pg/g wwa
p ; p 0-DDE,
pg/g wwa
p ; p 0-DDD,
pg/g wwa
PDDTs,
pg/gwwa
PBHC,
pg/g wwa
Baruthane (1) 290 2800 950 4040 22
Yesßil Fener (2) 400 300 850 1550 32
Kirmizi Fener (3) 240 70 2200 2510 290
Belediye Evleri (4) 1800 2400 1000 5200 4500Sinop (5) 1100 230 240 1570 4712
Yalikoy (6) nd 120 5400 5520 220
Owen Anchorageb 2
Rawsonc 2.02 6.99
Punto Loyolac 2.91 2.65
Punto Banderasc 59.58 6.59
Deer Islandc 73.32 2.7
Staten Islandc 119.41 3.16
Boston Horbourd 78
North Seae 116 68
Western Scheldte 240P
DDTs ¼ p ; p 0-DDTþ p ; p
0-DDD þ p ; p 0-DDE;
PBHC ¼ a-BHC þ b-BHC þ d-BHC þ c-BHC.
nd¼Not detected.a Bolded numbers are below detection limit.b Burt and Ebell (1995).c Report of Woods Hole Oceanographic Institution Coastal Research Center (1995).d Lauenstein (1995).e Cited in Cleemann et al. (2000).
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Sea. We hope that this study will be a starting point for
such kind of assessment and monitoring studies to
determine the level of pollution from chlorinated com-pounds in the region.
Acknowledgements
The authors are indebted to Dr. Jean Pierre Ville-
neuve (training officer in IAEA-MEL) and IAEA for
their help in supplying related papers, pesticide stan-
dards and experimental apparatus. We also would like
to thank to Prof. Kevin C. Jones (Lancaster University),
and Dr. Gareth O. Thomas (Lancaster University) for
their feedback. We are grateful to Dr. Feryal Ozturk
Akbal (Ondokuz Mayis University) for her endless help
and patience, and also thanks to all other people at theDepartment of Environmental Engineering of Akdeniz
University and Ondokuz Mayis University for their
support.
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0
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A
n o t d e t e
c t e d
EPA Human
Health Criteria32 pg/g-ww
EPA Wild Life
Criteria
200 pg/g-ww
pp'-DDE
120230300
2400
2800
70
0
500
1000
1500
2000
2500
3000
B a r u t h a n
e
Y e s i l F
e n e r
K i r m i z i F
e n e r
B e l e d i y e
E v l e r i
S i n o
p
Y a l i k
o y
Sampling Points
C
( p g / g - w w )
EPA Human
Health Criteria
32 pg/g-ww
EPA Wild
Life Criteria
200 pg/g-ww
B
pp'-DDD
5400
240
1000
2200
850950
0
5001000
1500
2000
2500
3000
3500
4000
45005000
5500
6000
B a r u t h a n
e
Y e s i l F
e n e r
K i r m i z i F
e n e r
B e l e d i y e
E v l e r i
S i n o
p
Y a l i k
o y
Sampling Point
C
( p g / g - w w )
EPA
Wild Life Criteria
200 pg/g-ww
EPA Human
Health Criteria
32 pg/g-ww
C
BHCs (Total)
22 32 220
47124500
290
0
500
1000
15002000
2500
3000
3500
4000
4500
5000
B a r u t h a n
e
Y e s i l F
e n e r
K i r m i z i F
e n e r
B e l e d i y e
E v l e r i
S i n o
p
Y a l i k
o y
Sampling Point
C
( p g / g - w w )
EPA Human
Health Criteria
100 pg/g-ww
EPA HumanHealth Criteria
9.9 pg/g-ww
< D e t e c t i o n
L i m i t
D
Dieldrin
780
180130
600
360380
0
500
1000
B a r u t h a n
e
Y e s i l F
e n e r
K i r m i z i F
e n e r
B e l e d i y e
E v l e r i
S i n o
p
Y a l i k
o y
Sampling Point
C
( p g / g
- w w ) EPA
Wild Life Criteria
22 pg/g-wwEPA Human
Health Criteria
0.65 pg/g-ww
E
HCB
180170
270
0
500
B a r u t h a n
e
Y e s i l F
e n e r
K i r m i z i F
e n e r
B e l e d i y e
E v l e r i
S i n o
p
Y a l i k
o y
Sampling Point
C
( p g / g
- w w )
EPA Human
Health Criteria
6.7 pg/g-ww
n o t d e t e c t e d
n o t d e t e c t e d
n o t d e t e c t e d
EPA Wild Life
Criteria
200 pg/g-ww
F
Fig. 2. Average concentrations of OCs (pg/g ww) in mussels and comparison with EPA criteria.
1082 P.B. Kurt, H.B. Ozkoc / Marine Pollution Bulletin 48 (2004) 1076–1083
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