7c

Environ Geochem Health (2007) 29:59–68 DOI 10.1007/s10653-006-9064-y

ORIGINAL PAPER

Distribution and bioaccumulation of organochlorine pesticides along the Black Sea coast Hu¨lya Boke Ozkoc Æ Gulfem Bakan Æ Sema Ariman

Received: 20 October 2005 / Accepted: 12 October 2006 / Published online: 4 January 2007
Springer Science+Business Media B.V. 2006

Abstract Sediment, mussel, and seawater samples were collected three times during 2001–2003 at nine sampling stations along the mid-Black Sea coast of Turkey. The samples were analyzed with GC-ECD for contents of various organochlorine pesticides (OCPs) in the environment. DDT and its metabolites were detected at concentrations significantly above the detection limits. The highest concentrations of DDT metabolites measured in the sediment and mussel samples were 35.9 and 14.0 ng/g wet weight respectively. Considerable levels of aldrin, dieldrin, endrin, heptachlor epoxide, lindane, endosulfan sulphate, and HCB were also detected in the sediment, mussel, or seawater samples. Although these persistent toxic compounds have been banned for some years in Turkey, they may still be used illegally in some regions, contributing to their significant levels in the environment. The biota– sediment accumulation factor (BSAF) estimated for DDT and its metabolites in mussels was 2.9, which is nearly two times higher than the benchmark of 1.7. In spite of such high BSAF values observed for these toxic compounds, their levels in mussels were significantly below the

H. B. Ozkoc
G. Bakan (&)
S. Ariman Department of Environmental Engineering, Faculty of Engineering, Ondokuz Mayıs University, 55139 Kurupelit, Samsun, Turkey e-mail: [email protected]

international legal limits recommended by the Food and Agriculture Organization of the United Nations. Edible biota from the waterbodies examined may thus still be considered safe for human consumption at this time. However, as pollutants can biomagnify through the food chain over time, further routine sampling and analysis of biota along the Black Sea coast are warranted in order to better assess the threat of OCPs to public health in the region. Keywords Sediment
Mussel
Organochlorine pesticides
Bioaccumulation
Biota-sediment accumulation factor
Black Sea
Biomagnification

Introduction The Black Sea is located between the European and Asian continents, and is connected to the Mediterranean Sea through the Sea of Marmara (Fig. 1). Its coastal environment is thus a place that potentially receives a considerable amount of pollutants from Turkey and neighboring countries (e.g. Bulgaria, Romania, Austria, the former USSR countries). Some of the prominent environmental pollutants are organochlorine pesticides (OCPs), which are not only toxic to humans, but also highly bioaccumulative due to their high lipophilicity and persistence. Comprehensive

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Fig. 1 Sampling stations at the rivers (S2, S4, S7, S9, S10) and on the midBlack Sea coast (SM3, SM5, SM6, SM8) of Turkey

studies across several countries or regions are needed to appreciate both the overall impacts of pollution with OCPs and their biological effects in the Black Sea area (Mee, 1992). It is noted that the control of OCP use was initiated back in the late 1970s in Turkey and Romania, but effective use restrictions were not imposed in Turkey until the early 1980s. There is indication that between 1976 and 1983, the annual use of organochlorine insecticides in Turkey was around 1,000 to 2,000 tonnes (Bakan & Ariman, 2004). At any rate, recent studies showed that DDT is still present in the rivers, streams, and waste disposals in Turkey ¨ zkoc¸, 2004; Bakan (Tuncer et al., 1998; Kurt & O & Ariman, 2004). In the meantime, there is speculation that some OCPs are still used considerably today in neighboring countries near the Black Sea area (Tanabe et al., 1997). Organochlorine pesticides can be concentrated as well as bioaccumulated in the environment through biogeochemical processes (e.g., Barbash, 2003). For example, marine and freshwater sediments can function as both a sink and a source for OCPs in the aquatic environment. They also serve as major repositories for OCPs and other persistent pollutants released into the aquatic environment (Doong, Sun, Liao, Peng, & Wu, 2002; Nhan et al., 1998). Since sediments provide good habitats for many small aquatic organisms,

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pesticide residues deposited on their surfaces will continue to be biologically available to humans and to wildlife that relies on the contaminated biota as food sources (Chapman, Ho, Munns, Solomon, & Weinstein, 2002). The present study was conducted to measure the OCP content in sediments and mussels from several areas along the mid-Black Sea coast of Turkey, with a subtle interest in the impacts that urban water run-off and sewage might have had on recent sediment quality in the Yes¸ ilırmak, Mert, Ku¨rtu¨n, Engiz, and Kızılırmak rivers. These OCP contaminants were assessed over a 2-year period between 2001 and 2003. In particular, levels of OCPs and their regional variations in sediments, mussels, and seawater were assessed and compared. Through use of the biota–sediment accumulation factor (BSAF), the present study also attempted to provide a bioavailability profile for these OCPs in aquatic biota. Although there are some recent studies related to organochlorine compounds in the region ¨ zkoc¸, 2004), (Bakan & Ariman, 2004; Kurt & O there has not been any work done on environmental pollution management and prevention for OCPs. Therefore, it is important for this study to continue monitoring OCP residues in sediments, mussels, and seawater, and to begin a series of surveys using BSAF to measure the

Environ Geochem Health (2007) 29:59–68

bioavailability of these pollutants along the midBlack Sea coast of Turkey. Sediments and mussels were used in the present study because they accumulate persistent pollutants at concentrations several orders of magnitude above those in water. Mussels are considered to be one of the standard biota indicators worldwide because of their abundance, ubiquity, sessile nature, long life span, and high filtration rates. The mussel Mytilus galloprovincialis is common in Turkey along the Black Sea coast due to the low seawater temperature and salinity available, which provide optimal conditions for the life and productivity of this species ¨ zkoc¸, 2004). Hence, this species was (Kurt & O used as the biota matrix in the present study. The BSAF is a screening tool used to predict the bioaccumulation potential of lipophilic compounds. Its value is simply calculated as the ratio of a pollutant’s lipid-normalized concentration in tissue of an aquatic organism to its organic carbon-normalized concentration in surface sediment. Bioaccumulation is implied when a BSAF is (significantly) greater than one. A theoretical value of 1.7 has been estimated based on partitioning of non-ionic organic compounds between tissue lipids and sediment carbon (ASTM, 1997). A value of less than 1.7 indicates less partitioning of an organic compound into lipids than predicted, whereas a value greater than 1.7 indicates more uptake of the compound than can be explained by the partitioning theory alone (Brunson, Confield, Dwyer, Ingersoll, & Kemble, 1998; US EPA, 1998).

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December 2001, once in October 2002, and once in January 2003. Individual surface sediment (each ~5-cm) samples (n = 9 in each sampling period) collected with a Bridge-Ekman grab sampler were well mixed and stored frozen (–20C) in pre-cleaned glass jars until analysis. Mussels of similar size (3.5–6.0 cm shell length) were stored in precleaned aluminum-coated containers and transported to the laboratory immediately after their collection in large numbers (UNEA/IAEA/IOC, 1996). Standard methods (APHA, AAWA, WPCF 1995) were used to collect and store seawater samples (n = 9 in each sampling period) during the same three sampling periods. Extraction Sediment and mussel samples were homogenized and extracted for analysis of OCPs using the standard Soxhlet’s method described in UNEP/ IOC/IAEA (1988). In essence, the dry weight (dw) to wet weight (ww) ratios of the sediments and mussels were determined. Each homogenate of 20 g was spiked with 25 ng/ml of the internal standards 2,4,5-TCB (trichlorobiphneyl) and c-HCH to quantify the overall extraction recovery. The sediment and mussel homogenates were each dried with anhydrous sodium sulphate and then extracted with 250 ml of hexane:dichloromethane mixture (1:1, v/v) of glass-distilled grade in a Soxhlet apparatus for 8 h. The dichloromethane and hexane were then combined and concentrated to about 15 ml by rotary evaporation and further evaporated to a few milliliters in a water bath at ~70C (UNEP/IOC/IAEA, 1988).

Materials and methods Clean-up Study area, sampling, and storage Figure 1 shows the nine sampling stations located at the rivers (stations S2, S4, S7, S9, S10) and on the mid-Black Sea coast (stations SM3, SM5, SM6, SM8) of Turkey. These stations were chosen specifically to include hotspots of pollution around Samsun City (e.g., the harbor region, industrial region, domestic wastewater discharge areas, and the rivers). Mussel, sediment, and seawater samples were collected once in

Prior to the extensive clean-up using a florisil column, mercury in the sediment extracts was removed through vigorous shaking; and lipid in mussels was extracted through treatment with concentrated sulphuric acid. From the florisil column (at 130C for 12 h), the first fraction eluted with 70 ml of hexane was used to concentrate HCB, DDE, heptachlor, and aldrin. The second fraction eluted with 50 ml of a freshly prepared mixture of hexane:dichloromethane

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(70:30, v/v) was for collection of DDD, DDT, and HCH. The third fraction containing endrin, dieldrin, endosulfan sulphate, and the remaining OCPs was eluted with 40 ml of dichloromethane. Forty milliliters of hexane was later added to the evaporation flask of the third fraction directly for solvent exchange. All fractions were further concentrated to about 1 ml in a waterbath before analysis (UNEP/IOC/IAEA, 1988). A blank sample was prepared with 30 g of pre-cleaned sodium sulphate to determine any contamination during analysis, and subjected to the same cleanup procedures as those applied to the mussel and sediment samples. Seawater samples were analysed using the liquid-liquid extraction procedure described in UNEP/IOC/IAEA (1988). These samples were applied in equal amounts with 240 ml of hexane in total in three steps. Before starting the extraction process, the water samples were each spiked with 25 ng/ml of the internal standards. A blank sample prepared with 240 ml of hexane was also included. After extraction, the same clean-up process used for the mussel and sediment samples were applied to the seawater samples, except without the mercury or the sulphuric acid treatment. Analysis and quantification After the clean-up, each fraction was injected into a GC-ECD system for chemical analysis. This system was equipped with an electron capture detector and split/splitless injector (Fissions HRGC Mega Series II). A capillary DB-5 column

Table 1 Average properties of surface sediments and mussels collected from selected areas along the mid-Black Sea coast of Turkey, 2001–2003*

* Locations of sampling stations are as described in Fig. 1; for the sediment samples, n = 27 in total; for mussels, collected in large numbers

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Sampling stations Black Sea SM3 SM5 SM6 SM8 Rivers S2 S4 S7 S9 S10

Sediment water content (%)

of 30 m · 0.32 mm (0.25-lm film thickness) was used for separation. The column oven temperature was programmed from 70C (initial time, 2 min) to 260C at a rate of 3C min–1, then kept at 260C for 90 min. Injector and detector temperatures were maintained at 250C and 300C respectively. Nitrogen was used as both the carrier (2 ml min–1) and the make-up (60 ml min–1) gas. The following reference standards, supplied by the International Atomic Energy Agency (IAEA, Laboratory of Marine Radioactivity, Monaco), were included in the analysis: HCB, a-HCH, b-HCH, d-HCH, c-HCH, heptachlor, aldrin, heptachlor epoxide, endosulfan-I, endosulfan-II, endosulfan sulphate, endrin, endrin aldehyde, dieldrin, lindane, pp-DDD, pp-DDE, and ppDDT. Concentrations of individual organochlorines were quantified by comparing peak areas of the samples with those of reference standards (UNEP/IOC/IAEA, 1988).

Results Pesticide residues in sediments The basic properties of the surface sediment samples are summarized in Table 1. The property parameters included were water and organic matter contents. The water and the organic matter contents in these sediment samples ranged from 23.1% to 39.4% and 2.9% to 30.1% respectively. The maximum organic matter of the sediment samples was observed at station S4,

Sediment organic matter (%)

Mussel average (shell length, cm)

Mussel average (shell width, cm)

23.13 39.39 32.06 28.29

3.23 3.88 2.98 2.92

4.1 4.3 3.3 3.7

7.0 6.8 6.5 6.3

38.71 25.74 27.12 28.78 31.07

4.77 30.10 16.77 13.82 11.47

– – – – –

– – – – –

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Table 2 Average concentrations (ng/g wet weight) of organochlorine pesticides in surface sediments from rivers and the mid-Black Sea coast of Turkey, 2001–2003a Sampling stations

Aldrin

Heptachlor epoxide

Dieldrin

Endrin

pp’DDT

pp’DDD

ppDDE

HCB

Lindane

Endosulfan sulphate

EOM

S2 SM3 S4 SM5 SM6 S7 SM8 S9 S10

2.637 5.388 3.228 <0.12 0.269 1.036 0.567 0.245 <0.12

<0.05 0.203 <0.05 <0.05 3.833 <0.05 9.917 0.105 <0.05

<0.12 5.032 <0.12 <0.12 <0.12 4.462 3.645 <0.12 <0.12

<0.15 11.738 0.469 5.032 <0.15 <0.15 7.831 0.289 <0.15

<0.18 0.346 0.662 <0.18 <0.18 <0.18 6.900 <0.18 <0.18

0.239 2.236 <0.18 <0.18 <0.18 <0.18 6.003 <0.18 35.904

<0.12 0.411 <0.12 <0.12 <0.12 <0.12 <0.12 <0.12 <0.12

<0.10 <0.10 <0.10 0.568 <0.10 <0.10 <0.10 <0.10 <0.10

15.138 <0.10 <0.10 <0.10 <0.10 7.523 <0.10 <0.10 <0.10

<0.10 <0.10 <0.10 25.007 2.256 <0.10 <0.10 <0.10 <0.10

1.205 2.223 19.410 4.117 2.383 2.115 1.383 2.43 1.235

a

Locations of sampling stations are as described in Fig. 1; those italicized are detection limits; EOM ” extractable organic matter (mainly lipid); n = 27 in total

located at the Mert river region of Samsun City, and was believed to be heavily polluted by direct discharge of domestic sewage waste water. There is considerable evidence indicating that organic matter is the predominant factor governing the adsorptivity of organochlorine compounds to sediments (Bakan & Ariman, 2004). As presented in Table 2, the following 10 organochlorine pesticide residues were detected in the sediment samples: pp-DDT, pp-DDD, ppDDE, aldrin, heptachlor epoxide, dieldrin, endrin, HCB, lindane (i.e., c-HCH), and endosulfan sulphate. Some of these levels exceeded the threshold effects concentrations (TECs) proposed as consensus-based sediment quality guidelines, which range from approximately 2 to 5 ng/g ww for most of the OCPs measured in the present study (MacDonald, Ingersoll, & Berger, 2000). The concentrations of pp-DDE and pp-DDT ranged from <0.12 (i.e., below the detection limit) to 0.4 and <0.18 (detection limit) to 6.9 ng/g ww respectively. The levels of pp-DDD were especially high, up to 35.9 ng/g ww. These results are similar to those observed in Bakan and Ariman (2004), and some are well above the consensusbased TECs. The higher levels of pp-DDD observed in the sediment samples suggest that this compound was once used as a pesticide on its own, rather than as a result of the metabolic transformation of ppDDT. After all, DDT in marine systems has a half-life of 5 years or longer (Villeneuve, Carvalho, Fowler, & Cattini, 1999), despite the fact that it can be transformed to DDE (under

oxidative conditions) or DDD (under anaerobic conditions). The concentrations of HCB in the sediment samples were relatively low (<0.1–0.6 ng/g ww). One explanation is that there is little recent use of this compound at the rivers or on the Black Sea coast. Another reason is that HCB has a relatively high vapor pressure (1.5 · 103 Pa), which may facilitate its volatization from water (Nhan et al., 1998). The concentrations of aldrin (5.4 ng/g ww), dieldrin (5.0 ng/g ww), and endrin (11.7 ng/ g ww) were highest at the coastal station SM3. The sediment concentrations of lindane were found to be below the detection limit in samples from all the stations except station S2 located at Yes¸ ilırmak River (15.1 ng/g ww) and station S7 at Ku¨rtu¨n River (7.5 ng/g ww). These high levels, while comparable to the high-end values in Japan observed by lwata, Tanabe, Sakai, Nishiura, & Tatsukawa (1994), suggest that lindane has been used near the two river areas. Pesticide residues in seawater The OCPs detected in the seawater samples include aldrin, heptachlor epoxide, dieldrin, endrin, pp-DDD, and HCB (Table 3). All of these concentrations were well below the maximum residue levels set for water quality criteria for toxic and deleterious substances in coastal and marine water (50 lg l–1 for DDTs and 4 lg l–1 for other OCPs; WHO, 1996). The highest water concentration detected was 0.5 lg l–1 (for

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Table 3 Concentrations (lg/l) of organochlorine pesticides in seawater samples from the mid-Black Sea coast of Turkey, 2001–2003a Sampling stations

Aldrin

Heptachlor epoxide

Dieldrin

Endrin

pp’DDT

pp’DDD

pp’DDE

HCB

Lindane

Endosulfan sulphate

SM3 SM5 SM6 SM8

0.166 <0.05 0.127 <0.05

0.293 0.496 0.525 <0.05

<0.01 <0.01 0.061 <0.01

<0.01 <0.01 0.02 <0.01

<0.01 <0.01 <0.01 <0.01

<0.01 0.077 0.371 <0.01

<0.01 <0.01 <0.01 <0.01

<0.05 0.034 0.188 <0.05

<0.01 <0.01 <0.01 <0.01

<0.01 <0.01 <0.01 <0.01

a

Locations of sampling stations are as described in Fig. 1; those italicized are detection limits; n = 27 in total

heptachlor epoxide at station SM6). The maximum residue levels recommended by WHO (1996) for both DDTs and HCH residues in water together is 1.0 lg l–1. The limits set by Europe for individual compounds and total pesticides in drinking water are 0.1 and 0.5 lg l–1 respectively (WHO, 1996). Pesticide residues in mussels The sizes (i.e., shell lengths and shell widths) of mussels collected for this study are summarized in Table 1. These samples were collected from four stations (SM3, SM5, SM6, and SM8) located on the mid-Black Sea coast. Of the 10 OCPs measured, pp-DDD appeared to be most abundant, with the highest concentration being 14.0 ng/ g ww (Table 4). The lipid contents (i.e., the extractable organic matter) of the mussel samples ranged from 31 to 72 ng/g ww. These results are ¨ zkoc¸ comparable to those reported by Kurt and O (2004). The concentrations of pp-DDE ranged from <0.12 (i.e., below the detection limit) to 0.23 ng/ g ww. These results are similar to those observed in ICES (1974). The international legal limit is 5 lg/g fresh weight (f.w.) for DDT and its metabolites in fish (Nauen, 1983; Haines, Brydges, MacDonald, Smith, & MacDonald, 1994; Maret & Dutton, 1999). The highest concentration of HCB measured in mussels was 0.4 ng/g ww, which is far below the US EPA Screening Criteria of 70 ng/g ww (US EPA, 1995; Maret & Dutton, 1999). This finding suggests that at least in recent years, little of this pesticide was applied near the rivers or on the coast. The HCB residues detected in this coastal area were probably transported atmospherically

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from nearby cities where large amounts of technical HCB were still being used (Guruge & Tanabe, 2001; Nhan et al. 1998). The levels of dieldrin and aldrin were below the detection limits at all stations except for aldrin at station SM3 (measuring 0.9 ng/g ww). The levels of heptachlor epoxide, lindane, and endosulfan sulphate were also well below the US EPA Screening Criteria. The highest concentrations for these three compounds were 2.4, 1.5, and 0.8 ng/g ww respectively. Although the use of HCHs in agriculture has been greater compared with DDT, the relatively lower concentrations of lindane measured in mussels reflect their lower potential for bioaccumulation in aquatic biota. The more rapid decline of HCH concentrations in the marine environment is actually in good agreement with the higher hydrolysis rates known for these compounds (Villeneuve et al., 1999). Bioaccumulation profiles of OCPs on the Black Sea coast The BSAFs calculated in this study, except for DDTs, were well below 1.0, suggesting that the theoretical value of 1.7 could be used to predict the BSAF for most OCPs with a reasonable degree of comfort or health conservatism. The BSAF for DDTs (including its metabolites) was 2.9, which is significantly greater than the theoretical cut-off point (benchmark) of 1.7. This higher BSAF for DDTs in biota on the mid-Black Sea coast may be due to the exposure to contaminants in the overlying water, to the spatial differences in sediment contamination, or to the taxonomic-specific differences in exposure. Bioconcentration factors (BCF) for OCPs in mussels were estimated based on the ratio of the

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Table 4 Average concentrations (ng/g ww) of organochlorine pesticides in mussels from the mid-Black Sea coast of Turkey, 2001–2003a Sampling stations

Aldrin Heptachlor epoxide

Dieldrin Endrin pp’DDT

pp’DDD

SM3 SM5 SM6 SM8

0.879 <0.05 <0.12 <0.05 <0.12 2.419 <0.12 0.388

<0.12 <0.12 <0.12 <0.12

<0.18 <0.12 0.364 <0.10 1.179 <0.12 <0.10 <0.10 3.576 0.230 <0.10 <0.10 14.015 0.228 <0.10 1.511

7.782 0.205 <0.15 <0.15

<0.18 <0.18 <0.18 <0.18

pp’DDE

HCB

Lindane Endosulfan sulphate <0.10 0.800 <0.10 <0.10

EOM 50.506 49.423 30.686 71.730

a

Locations of sampling stations are as described in Fig. 1; those italicized are detection limits; EOM ” extractable organic matter (mainly lipid); a large number of mussels (n > 30) were collected and used

Table 5 Biota–sediment accumulation factor (BSAF) and bioconcentration factor (BCF) determined for organochlorine pesticides (OCPs) in mussels from the mid-Black Sea coast of Turkey OCPs

BSAF

BCF

Aldrin Heptachlor epoxide Endrin DDTs HCB Endosulfan sulphate

0.420 0.302 0.487 2.864 0.641 0.059

6.0 3.2 199.7 28.2 3.3 –

concentration in the aquatic organism to that in seawater. This parameter describes the ability of a chemical to concentrate in aquatic organisms. By convention, a BCF value lower than 250 is considered as having a low potential for bioconcentration. As shown in Table 5, endrin had the highest BCF value of 200. Discussion and conclusions This study documented the analysis of organochlorine pesticide residues in sediments, mussels, and seawater from the Kızılırmak (S10), Yesilırmak (S2), Mert (S4), Ku¨rtu¨n (S7), and Engiz (S9) river catchment areas and from the immediate marine coastline of the mid-Black Sea region. The residues detected were aldrin, heptachlor epoxide, endosulfan sulphate, endrin, dieldrin, lindane, HCB, pp-DDE, pp-DDD, and pp-DDT. Consensus-based no-effect threshold values recommended for total DDTs and most other OCPs measured in the present study are 5.3 and 1.9– 4.9 lg/kg dw (at 1% total organic carbon) respectively (MacDonald et al,, 2000). The levels of total DDT residues measured at some sites (e.g.,

Samsun City, 2.5 ng/g ww; Kızılırmak River, 35.9 ng/g ww) were near or well above these TECs set for protecting human health, especially when dw is taken into consideration. Hence, there is a potential risk that the sediments from some areas would be harmful to humans. The sediment levels of DDTs and lindane measured in this study were higher than those in other countries (Table 6). On the other hand, the DDT levels measured in the mussels from this study were largely comparable to those observed in other countries or regions except Sri Lanka (Table 7). These data thus suggest that there has been more recent use of DDT in the Black Sea area. This seems to be especially the case around the coast (SM3) and the Mert river (S4) areas where the ratios of DDT:DDE measured in sediments were nearly 1 or greater (Table 2). The DDT:DDE ratio is expected to be much lower than 1 if DDT has not been used recently (since its metabolite DDE is more stable and persistent in the environment). Furthermore, DDT compounds with lower vapor pressures (0.2–8.0 · 10–5 Pa) are not subject to much volatilization or transport in the vapor phase (Nhan et al., 1998). The levels of total DDT residues measured in mussels in this study (<0.12–14.0 ng/g) were far below the international legal limit of 5,000 ng/g f.w. for removing fish (and other seafoods) from marketplace for the protection of human health (Nauen, 1983; Haines et al., 1994; Maret & Dutton, 1999). The c-HCH concentrations measured in the mussels were also well below those legal limits for human health set in Canada (100 ng/g f.w.) or in Germany (2,000 ng/g f.w.) for fish and fisheries products (Haines et al., 1994,

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Table 6 Comparison of study results on sediment levels (ng/g wet or dry weight.) of DDTs, HCHs, and polychlorinated biphenyls (PCBs) from various geographical locations Site (country)

DDTs

HCHs

PCBa

Reference

Mediterranean Negombo, Sri Lanka North coast Vietnam Victoria harbor, Hong Kong Cities, India Cities, Japan Bosphorus, Black Sea, Turkey Sochi, Black Sea, Russia Coastline, Black Sea, Ukraine Yes¸ ilırmak river, Turkey Black Sea coast of Samsun, Turkey Kızıırmak river, Turkey Yes¸ ilırmak river, Turkey Mert stream, Turkey Black Sea coast of Samsun, Turkey

0.05 0.4 6.2–10.4 1.4–97 8–450 2.5–12 0.2–7.2 3.3–12 0.06–0.6 7 18–55 35..9 0.2 0.7 2.1

0.01 0.1 1.2–33.7 <0.1–9.4 0.6–38 4.5–6.2 0.08–1.1 0.3–0.8 0.02–0.2 <0.05 5–16 1.9 15.1 <0.1 <0.1

0.8 1.1 0.5–28.1 3.2–81 4.8–1000 63–240 0.4–44 0.3–4.7 ND-0.4 NA NA NA NA NA NA

Iwata et al. (1994) Guruge and Tanabe (2001) Nhan et al. (1999) Hong et al. (1995) Iwata et al. (1994) Iwata et al. (1994) Filmann et al. (2002) Filmann et al. (2002) Filmann et al. (2002) Bakan and Ariman (2004) Bakan and Ariman (2004) This study This study This study This study

a

ND: not detected; NA: not available

Table 7 Comparison of study results on organochlorine pesticide (OCP) concentrations (ng/g wet weight) in mussels from various geographical locations Location

Mussel

OCP pollutant

Range

Reference

NW Mediterranean coast

My tilus galloprovincialis

Mutilus edulis Mutilus edulis

Egyptian

Musse l

Negombo, Sri Lanka Sinop, Turkey

Musse l My tilus galloprovincialis

Yalikoy, Turkey

My tilus galloprovincialis

Samsun city harbor, Turkey

My tilus galloprovincialis

Samsun city harbor, Turkey

My tilus galloprovincialis

20–360 1.8–3.6 0.8–3.1 6.7–960 1.1–19.5 0.06–1.19 98.1–629.8 2.2–58.7 2.4–40.3 5.7 1.570 4.712 5.520 0.220 0.364 7.782 14.015 0.388

Villeneuve et al. (1999)

USA Korea

DDTs Dieldrin Lindane DDTs DDTs HCHs DDTs Dieldrin Aldrin DDTs DDTs BHCs DDTs BHCs HCB Endrin DDTs Heptachlor epoxide

Table 6). Therefore, in spite of the high BSAF values determined for DDTs, edible biota from the water bodies examined are still considered safe for human consumption at this time. It must be noted, however, that mussels are not a preferred seafood for Turkish people. The levels of contamination detected in this study may still be a threat to public health over time, since fish is the most common seafood in the region. Furthermore, bioaccumulation only

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Sericano et al. (1995) Khim et al. (2000) Khaled et al. (2004)

Guruge and Tanabe (2001) ¨ zkoc¸ (2004) Kurt and O ¨ zkoc¸ (2004) Kurt and O This study This study

provides an index on how or how much pollutants enter a food chain. Pollutants can biomagnify as they move from one trophic level to the next in the food chain. Thus, when (large) fishes in the aquatic food chain are taken into consideration, pollution with OCPs in the region over time may ¨ zkoc¸, still be a threat to public health (Kurt & O 2004). It is due to concern over biomagnification with fish consumption that further routine sampling and analysis of biota along the Black Sea

Environ Geochem Health (2007) 29:59–68

coast are warranted in order to better appreciate the ultimate health impact of OCPpollution in this region. Acknowledgement This study has been supported _ financially through TUBITAK (The Scientific and Technical Research Council of Turkey) under Project No. YDABAG–100Y110.

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