XiaoLi Huangab,
DongLi Qinb,
Lei Gaob,
Qirui Haob,
Zhongxiang Chenb,
Peng Wangb,
Shizhan Tangb,
Song Wub,
Haifeng Jiangb and
Wei Qiu*ac
aState Key Laboratory of Urban Water Resource and Environment, Harbin Institute of Technology, 150090, Harbin, Heilongjiang, China. E-mail: qiuweihit@126.com
bHeilongjiang River Fisheries Research Institute, Chinese Academy of Fishery Sciences, 150070, Harbin, Heilongjiang, China
cSchool of Municipal & Environmental Engineering, Harbin Institute of Technology, 150090, Harbin, Heilongjiang, China
First published on 16th October 2019
This study aimed at investigating the accumulation and potential risks of eight metal(loid)s in fish from natural and culturing water samples in Northeast China. Chromium (Cr), nickel (Ni), copper (Cu), zinc (Zn), arsenic (As), cadmium (Cd), lead (Pb) and mercury (Hg) contents in 16 fish species (155 samples) and sediments of their habitats were analyzed. In general, the concentrations of these eight metal(loid)s in most fish samples are lower than the guideline levels and legal limits, and the Pb and Hg level in 0.65% of samples were exceeded the quality standards in China. The Cr, As, Cd and Pb levels in most fish samples are less than those reported in previous studies. Nonetheless, Hg levels in these fish samples are significantly higher than those reported in previous studies conducted in other regions. Different from the wild fish, significant positive correlations are found between Cr, Ni, As and Cd concentrations in cultured fish and those in pond sediment (P < 0.05), which might be due to the closed static water environment and concentrated feeding operations. Cu, Zn, As and Hg concentrations differed significantly among wild species, while Cu and Zn concentrations differed significantly among cultured species (P < 0.05), which might be because of the different feeding and foraging habitats. The target hazard quotients (THQs) at high exposure levels of target metal(loid)s in the studied fish were below 1 (except for Hg), and the carcinogenic risk indices of Cr, As, and Cd were less than 10−4. The levels of metal(loid)s (except for Hg) in the studied fishes fell within an acceptable range, but more attention should be paid to the potential carcinogenic risks.
In general, heavy metal levels in a fish are related to its living environment, feeding behavior and foraging habitats.17,18 There are numerous studies on the relationship between heavy metal pollution in the environment and in fish. For instance, sediment acts as an important sink for heavy metals, which affects the heavy metal bioconcentration by affecting bioavailability.19 Because of the biogeochemical characteristics and pathways of trophic transfer, the metal burdens in food web components are different, which lead to the difference in individual fish taxa by functional feeding groups.20,21 Previous studies have suggested that the foraging habitat is a strong predictor for variations in heavy metal concentrations in fish.21 While heavy metal contamination of freshwater and marine biota in China has been well described,10,12,17,18,22 such investigations are rather limited in Northeast China. Some heavy metals (i.e., As, Cd, Pb and Hg) are of major environmental concern as they can cause severe health implications for humans and other living organisms. Moreover, some elements (e.g., Cr, Ni, Cu and zinc (Zn)) that play essential roles in life activities become toxic in excess amounts.
Northeast China is a water-rich area with satisfactory water resource conditions and long fishing history, especially the Amur River basin, which contains a rich freshwater ecosystem with various fish species from the frigid-zone, temperate zone and even the tropical zone. In Northeast China, aquatic environments such as rivers, lakes, artificial reservoirs and ponds provide all types of aquaculture. However, many major cities and chemical enterprises in Northeast China are located near rivers and lakes, where the released waste threatens these aquatic ecosystems. Recently, two serious environmental contamination accidents have occurred in the Songhua River, which is the third-largest river in China and one of the biggest tributaries of the Amur River.23,24 Studies have found elevated heavy metal concentrations in the water and sediment in some rivers and lakes in Northeast China.25–27 Studies have been conducted to investigate the trace elements in the tissues of fish from fish farms28 and individual rivers or areas in Northeast China.29 Nonetheless, little is known about the heavy metal levels in fish from Northeast China, particularly for various species with different feeding habits, and the relationship between heavy metals and the environment.
This study aims to develop a large-scale analysis to compare eight metal(loid) levels (including Cr, Ni, Cu, Zn, As, Cd, Pb and Hg) in fish from different water types in Northeast China, investigate the relationship between heavy metals and the environment as well as evaluate the potential health risks associated with fish consumption.
Scientific name | English name | n | Feeding habits | Foraging habitats | The total length (cm) | Body weights (kg) |
---|---|---|---|---|---|---|
a n means the number of samples. | ||||||
Hypomesus olidus | Pond smelt | 1 | Omnivory | Pelagic fishes | 10.20 | 0.0085 |
Esox reicherti | Amur pike | 6 | Sarcophagy | Pelagic fishes | 50.60 ± 2.40 (47.00–55.00) | 0.64 ± 0.14 (0.52–0.91) |
Leuciscus waleckii | Amur ide | 3 | Omnivory | Pelagic fishes | 23.90 ± 3.60 (19.00–29.00) | 0.14 ± 0.093 (0.035–0.28) |
Ctenopharyngodon idellus | Grass carp | 19 | Herbivority | Middle-lower layers fishes | 53.00 ± 11.20 (38.00–72.00) | 1.93 ± 1.14 (0.71–4.23) |
Hemibarbus labeo | Barbell steed | 2 | Omnivory | Bottom fishes | 26.00 ± 4.90 (22.50–29.50) | 0.16 ± 0.09 (0.095–0.23) |
Hemibarbus maculatus | Spotted steed | 1 | Omnivory | Middle-lower layers fishes | 28.00 | 0.22 |
Saurogobio dabryi | Chinese lizard gudgeon | 1 | Omnivory | Middle-lower layers fishes | 13.70 | 0.031 |
Erythroculter ilishaeformis | Topmouth culter | 7 | Sarcophagy | Pelagic fishes | 54.90 ± 8.50 (42.00–69.00) | 1.23 ± 0.46 (0.71–2.06) |
Erythroculter mongolicus | Mongolian redfin | 1 | Sarcophagy | Pelagic fishes | 24.50 | 0.22 |
Cyprinus carpio | Common carp | 39 | Omnivory | Bottom fishes | 42.80 ± 7.40 (29.00–61.00) | 1.29 ± 0.87 (0.32–4.40) |
Carassius auratus | Crucian carp | 36 | Omnivory | Bottom fishes | 21.80 ± 5.50 (8.80–29.00) | 0.22 ± 0.14 (0.019–0.47) |
Hypophthalmichthys molitrix | Silver carp | 11 | Filter feeder (zooplankton, phytoplankton) | Pelagic fishes | 47.30 ± 11.90 (26.00–61.00) | 1.22 ± 0.86 (0.15–3.65) |
Aristichthys nobilis | Bighead carp | 12 | Filter feeder (zooplankton, phytoplankton) | Pelagic fishes | 51.20 ± 9.40 (33.00–64.00) | 2.16 ± 1.13 (0.45–4.19) |
Pseudobagrus fulvidraco | Yellow catfish | 2 | Omnivory | Bottom fishes | 15.10 ± 3.40 (12.70–17.50) | 32.0 ± 2.83 (30.0–34.0) |
Parasilurus asotus | Sheatfish | 13 | Sarcophagy | Bottom fishes | 37.00 ± 9.40 (25.00–50.00) | 0.41 ± 0.36 (0.10–1.38) |
Protosalanx hyalocranius | Clearhead icefish | 1 | Sarcophagy | Pelagic fishes | 14.50 | 0.025 |
When the THQ value is less than one, there should be no obvious non-carcinogenic risks for the exposed population. Otherwise, the exposed population would experience adverse health risks. Such concerns would further increase with a higher THQ value.
Heavy metals | Min. | Max. | Mean | Standard deviation | Median | Detection rate (%) | Maximum levels (MLs) for heavy metals in fish | Over-limit ratiob (%) | |||
---|---|---|---|---|---|---|---|---|---|---|---|
Quality standard in China | Commission regulation (EC) | FAO | DHO | ||||||||
a n means the number of muscle samples.b According to the quality standard in China.c ND: Not detected, means the value is lower than the limit of detection. Concentrations less than the LOD were set to ½ LOD for statistical analysis.d GB 2762-2017 National Food Safety Standard Maximum Levels of Pollutants in Foods (in Chinese).34 The maximum level for predatory fish is 1.00 mg kg−1, but for all other fish it is 0.50 mg kg−1.e NY 5073-2006 Limited Quantity of Poisonous and Harmful Contents of the National Pollution-Free Aquatic Products (in Chinese).35f The maximum level for predatory fish including swordfish is 1.00 mg kg−1 but for all other fish and processed fish, it is 0.50 mg kg−1. | |||||||||||
Cr | NDc | 0.49 | 0.018 | 0.048 | 0.019 | 33.55 | 2.00d | 0 | |||
Ni | ND | 0.78 | 0.019 | 0.069 | 0.039 | 19.35 | |||||
Cu | 0.067 | 0.97 | 0.27 | 0.13 | 0.25 | 100.00 | 50e | 30 | 0 | ||
Zn | 2.49 | 51.38 | 7.97 | 6.05 | 5.94 | 100.00 | 30 | ||||
As | ND | 0.39 | 0.052 | 0.054 | 0.039 | 97.42 | 0.10d | 3.00 | 10.97 | ||
Cd | ND | 0.009 | 0.0012 | 0.0013 | 0.0010 | 48.39 | 0.10d | 0.05 | 0.05 | 1.00 | 0 |
Pb | ND | 0.70 | 0.034 | 0.074 | 0.024 | 70.97 | 0.50d | 0.30 | 0.20 | 0.50 | 0.65 |
Hg | ND | 0.82 | 0.079 | 0.14 | 0.057 | 74.19 | 0.50/1.00d | 0.50 | 0.50/1.00f | 0.50/1.00f | 0.65 |
The results presented here are comparable to the studies conducted elsewhere, which also reported Cu and Zn to be the most abundant compounds among detected chemical elements (Table 3).17,18,39–41 The concentrations of Cr, As, Cd and Pb in most of the samples are either less than previous studies10,11,22,39,40,42 or undetected. Hg concentrations of fish in this study are higher than those from the Yellow River Estuary,10 South China Sea,12 East China Sea43 and Yangtze River,44 confirming heavy metal pollution in the waters of Northeast China.
Location | Number of fish species | Cr | Ni | Cu | Zn | As | Cd | Pb | Hg | References |
---|---|---|---|---|---|---|---|---|---|---|
a Wet weight.b Dry weight.c ND means not detected. | ||||||||||
Northeast of Chinaa | 16 | NDc–0.49 | ND–0.78 | 0.067–0.97 | 2.49–51.38 | ND–0.39 | ND–0.009 | ND–0.70 | ND–0.82 | Present study |
Bangshi River (Bangladesh)b | 0.47–2.07 | 8.33–43.18 | 42.83–418 | 1.97–6.24 | 0.09–0.87 | 1.76–10.27 | 39 | |||
Yangtze River (China)a | 0.10–0.24 | 0.77–1.22 | 2.8–7.55 | NA | 0.046–0.12 | 0.21–0.81 | 18 | |||
Pearl River (China)a | 13 | 0.11–4.27 | 0.15–7.55 | 8.78–30.3 | NA | 0.01–0.13 | 0.09–30.70 | 40 | ||
Nam Co Lake, Yamdro Lake and Lhasa River (China)a | 7 | 0.094–0.22 | 0.33–2.0 | 2.5–6.9 | 0.067–0.27 | 0.013–0.029 | 0.024–0.079 | 41 | ||
Taihu Lake (China)a | 1 | 0.12–0.50 | 0.39–1.47 | 0.02–0.11 | 0.35–1.20 | 17 | ||||
Yellow River Estuary (China)a | 11 | 0.01–0.87 | 0.01–0.22 | 10 | ||||||
Pearl River Delta (China/Hong Kong)a | 11 | 0.20–0.65 | 0.79–2.26 | 15.20–29.50 | 0.03–1.53 | 0.02–0.06 | 0.03–8.62 | 22 | ||
Hainan coastal area, South China sea (China)a | 1.38–4.36 | 0.07–0.94 | 1.45–8.07 | 0.48–6.99 | ND–0.012 | 0.02–0.05 | 12 | |||
Western continental shelf of South China Sea | 4 | 0.86–2.89 | 0.48–0.78 | 0.39–2.65 | 11.75–15.59 | 0.027–0.15 | 0.54–2.17 | 11 | ||
Northeast Mediterranean Sea (Europe)b | 6 | 1.24–2.42 | 2.34–4.41 | 16.5–37.4 | 0.37–0.79 | 2.98–6.12 | 42 |
Fig. 2 The target metal(loid) concentrations in wild fish from natural waters and cultured fish from aquaculture ponds. |
The relationship between metal(loid) concentrations in fish and in their living environment is shown in Fig. 3. The target metal(loid) concentrations in wild fish are not correlated to those in the sediment of their living environment (except for Cd). Cd concentrations in wild fish samples were positively correlated to Cd levels in the sediments of nature water (R2 = 0.081, P = 0.012). Positive correlations were observed between Cr, Ni, As and Cd concentrations in the cultured fish and in pond sediment (R2 = 0.099, R2 = 0.070, R2 = 0.038 and R2 = 0.145, respectively, P < 0.05 for all tests). However, correlations between Cu, Zn, Pt and Hg concentrations in cultured fish and those in pond sediment were relatively weak (R2 = 0.022, R2 = 0.044, R2 = 0.025 and R2 = 0.004, in order, P > 0.05 for all tests).
Metal(loid)s in the fish samples analyzed in this study are closely related to their living environment.10 In the closed static water environment, cultured fish can absorb the essential elements Cr, Ni, Cu and Zn from aquaculture feed, which results in higher levels and detection rates. This may explain why Cr and Ni levels in cultured fish tend to correlate with those in the pond sediment (mainly composed of feed bait, excrement, plankton particles and other suspended matter). Ponds investigated in this study usually use groundwater or clean spring water as the aquaculture water source. Thus, the significant relationship between the As and Cd concentrations in cultured fish and in pond sediment may indicate that As and Cd in cultured fish originate from the aquaculture feed. The potential routes of metal(loid)s entering a fish include food and non-food particle intake, surface absorption by fish tissues (gill, skin and body mucus) and oral consumption of water.8,45
Relative to wild fish, the higher detection rates and levels of Pb in cultured fish are the results of compounded effects from the aquaculture feed and water environment. Metal(loid)s in fish can reflect the water environmental pollution to a certain extent.10,14 The detection frequency of As in cultured fish was similar to that in fish from natural water, while the As concentration was significantly lower than in wild fish, which indicated As-pollution in natural waters. The Songhua River in Northeastern China is one of the representative Hg-polluted rivers in China.23 About 149.8 t of Hg from the Jilin chemical plant had been directly discharged into the Songhua River in 1958–1971. Studies on Hg pollution of fish and sediment in the Songhua River and health concerns of local residents have been uninterrupted over the past 40 years.25,46,47 Recent research showed that the T-Hg pollution level of the Second Songhua River was moderate to severe with high ecological risk, and the pollution levels in the main stream of the Songhua River were mild with low ecological risk.26 As mentioned above, the Hg levels in wild fish in this study are significantly higher than in the cultured fish (P < 0.0001), confirming the high level of Hg pollution and the potential ecological risk of natural waters.
Scientific name | Cr | Ni | Cu | Zn | As | Cd | Pb | Hg | |
---|---|---|---|---|---|---|---|---|---|
a ND means not detected. | |||||||||
Carassius auratus | Cultured | 0.027 ± 0.043 (ND–0.15) | 0.028 ± 0.050 (ND–0.20) | 0.34 ± 0.20 (0.15–0.97) | 7.93 ± 3.65 (3.83–18.44) | 0.035 ± 0.030 (0.003–0.14) | 0.0008 ± 0.0006 (ND–0.003) | 0.031 ± 0.013 (0.015–0.067) | 0.003 ± 0.005 (ND–0.018) |
Wild | 0.040 ± 0.12 (ND–0.49) | 0.018 ± 0.030 (ND–0.12) | 0.37 ± 0.15 (0.12–0.55) | 16.59 ± 11.57 (4.94–51.38) | 0.075 ± 0.069 (0.009–0.28) | 0.002 ± 0.002 (ND–0.008) | 0.020 ± 0.021 (ND–0.071) | 0.082–0.085 (0.001–0.26) | |
Cyprinus carpio | Cultured | 0.026 ± 0.041 (ND–0.13) | 0.008 ± 0.009 (ND–0.035) | 0.20 ± 0.067 (0.12–0.35) | 6.12 ± 2.71 (3.20–13.74) | 0.037 ± 0.034 (ND–0.13) | 0.0008 ± 0.0006 (ND–0.003) | 0.032 ± 0.02 (0.014–0.085) | 0.041 ± 0.18 (ND–0.82) |
Wild | 0.0072 ± 0.0098 (ND–0.031) | 0.006 ± 0.002 (ND–0.011) | 0.29 ± 0.12 (0.12–0.46) | 12.40 ± 8.44 (4.30–29.74) | 0.049 ± 0.041 (0.01–0.27) | 0.002 ± 0.001 (ND–0.004) | 0.044 ± 0.11 (ND–0.70) | 0.095–0.053 (ND–0.18) | |
Ctenopharyngodon idellus | Cultured | 0.022 ± 0.037 (ND–0.16) | 0.061 ± 0.19 (ND–0.78) | 0.31 ± 0.095 (0.20–0.50) | 8.77 ± 4.53 (4.53–20.01) | 0.042 ± 0.030 (0.003–0.14) | 0.0006 ± 0.0004 (ND–0.002) | 0.082 ± 0.11 (ND–0.43) | 0.005 ± 0.006 (ND–0.019) |
Wild | ND | ND | 0.25 ± 0.21 (0.11–0.40) | 9.26 ± 7.26 (4.13–14.39) | 0.074 ± 0.045 (0.042–0.11) | ND | 0.036 ± 0.031 (0.014–0.058) | 0.010 ± 0.013 (ND–0.019) | |
Esox reicherti | Wild | 0.005 ± 0.005 (ND–0.014) | ND | 0.18 ± 0.11 (0.074–0.39) | 4.50 ± 0.77 (4.61–5.73) | 0.085 ± 0.086 (0.027–0.26) | 0.0013 ± 0.001 (ND–0.003) | 0.004 ± 0.003 (ND–0.01) | 0.37 ± 0.099 (0.27–0.56) |
Pseudobagrus fulvidraco | Wild | 0.013 ± 0.015 (ND–0.023) | ND | 0.25 ± 0.12 (0.16–0.33) | 7.47 ± 3.43 (5.04–9.89) | 0.013 ± 0.006 (0.008–0.017) | 0.002 ± 0.001 (0.001–0.003) | 0.022 ± 0.002 (0.02–0.023) | 0.080 ± 0.004 (0.077–0.082) |
Hypophthalmichthys molitrix | Cultured | 0.0025 | 0.005 | 0.46 | 9.78 | 0.02 | 0.0005 | 0.019 | ND |
Wild | 0.005 ± 0.006 (ND–0.019) | 0.011 ± 0.013 (ND–0.046) | 0.28 ± 0.10 (0.14–0.48) | 4.28 ± 2.22 (2.78–10.33) | 0.072 ± 0.030 (0.029–0.13) | 0.0006 ± 0.0002 (ND–0.001) | 0.015 ± 0.028 (ND–0.079) | 0.11 ± 0.10 (0.005–0.27) | |
Parasilurus asotus | Wild | 0.016 ± 0.042 (ND–0.15) | 0.015 ± 0.027 (ND–0.10) | 0.20 ± 0.079 (0.086–0.40) | 5.28 ± 1.93 (2.77–10.55) | 0.015 ± 0.018 (ND–0.052) | 0.001 ± 0.001 (ND–0.004) | 0.016 ± 0.012 (ND–0.042) | 0.12 ± 0.11 (ND–0.32) |
Erythroculter ilishaeformis | Wild | 0.011 ± 0.014 (ND–0.04) | ND | 0.23 ± 0.072 (0.15–0.35) | 5.17 ± 1.01 (3.27–6.08) | 0.034 ± 0.013 (0.018–0.050) | 0.002 ± 0.002 (ND–0.005) | 0.030 ± 0.044 (ND–0.12) | 0.36 ± 0.25 (0.057–0.63) |
Leuciscus waleckii | Wild | ND | ND | 0.29 ± 0.059 (0.23–0.34) | 5.56 ± 0.73 (4.72–6.05) | 0.072 ± 0.016 (0.062–0.09) | 0.0008 ± 0.0003 (ND–0.001) | 0.004 ± 0.003 (ND–0.008) | 0.057 ± 0.030 (0.023–0.075) |
Aristichthys nobilis | Cultured | 0.023 ± 0.036 (ND–0.065) | 0.016 ± 0.019 (ND–0038) | 0.24 ± 0.053 (0.18–0.28) | 5.38 ± 2.18 (3.28–7.64) | 0.053 ± 0.030 (0.034–0.087) | 0.0007 ± 0.0003 (ND–0.001) | 0.037 ± 0.18 (0.019–0.054) | ND |
Wild | 0.004 ± 0.004 (ND–0.015) | 0.028 ± 0.068 (ND–0.21) | 0.22 ± 0.068 (0.13–0.33) | 4.55 ± 1.325 (2.49–6.76) | 0.060 ± 0.048 (ND–0.16) | 0.001 ± 0.001 (ND–0.004) | 0.006 ± 0.007 (ND–0.024) | 0.068 ± 0.049 (ND–0.17) | |
Hemibarbus labeo | Wild | ND | ND | 0.38 ± 0.26 (0.20–0.56) | 5.65 ± 0.96 (4.97–6.32) | 0.042 ± 0.016 (0.03–0.053) | 0.002 ± 0.0007 (0.001–0.002) | 0.011 ± 0.012 (ND–0.02) | 0.090 ± 0.053 (0.052–0.13) |
Hypomesus olidus | Wild | ND | ND | 0.26 | 24.01 | 0.39 | 0.007 | ND | 0.008 |
Protosalanx hyalocranius | Wild | ND | ND | 0.067 | 9.52 | 0.059 | 0.004 | ND | ND |
Hemibarbus maculatus | Wild | ND | ND | 0.24 | 5.51 | 0.066 | 0.001 | ND | 0.12 |
Erythroculter mongolicus | Wild | 0.005 | ND | 0.18 | 5.57 | 0.039 | ND | 0.01 | 0.13 |
Saurogobio dabryi | Wild | ND | ND | 0.25 | 14.56 | 0.050 | 0.009 | 0.007 | 0.065 |
Fish species are one of the most important drivers for metal(loid) accumulation, probably because of different feeding habits and foraging habitats of the studied fish. Dietary habits would affect the concentrations of the toxic elements As and Hg in fish from Northeast China. Relatively high As levels are observed in wild filter-feeding (Hypophthalmichthys molitrix and Aristichthys nobilis) and omnivory (Carassius auratus and Cyprinus carpio) fish, while the wild sarcophagi fish (Parasilurus asotus and Erythroculter ilishaeformis) had lower As concentration. Differences in As levels among wild fish species could be due to trophic transfer in the food web/sources.48 The Hypophthalmichthys molitrix and Aristichthys nobilis were strictly planktivorous and were expected to acquire As from small plankton and zooplankton. Carassius auratus and Cyprinus carpio do not feed exclusively on the small plankton and zooplankton but also feed on benthic animals. Parasilurus asotus and Erythroculter ilishaeformis are carnivorous and feed on small fishes. Chen and Folt20 reported that As could be elevated in lower trophic levels, and lower trophic feeders in the fish feeding strategy experiment would have higher metal burdens (planktivores > omnivores and piscivores). Notably, higher As is found in the muscle of the omnivorous fish, Carassius auratus, which could be due to both the foraging habitat and feeding habits. Similar to previous studies, the current study has found that the Hg concentration in wild sarcophagi fish is higher than that in omnivores and filter-feeding. Many studies also reported evidence of the biomagnification and bioaccumulation of mercury with trophic levels.13,15,49 Particularly, total mercury burdens in muscle tissue are a result of biomagnification through the food web rather than bioaccumulation.15
Elements | RfDs, μg per kg per day | Average exposure level | High exposure level | CRI (10−6) | ||
---|---|---|---|---|---|---|
EDI, μg per kg per day | THQ | EDI, μg per kg per day | THQ | |||
a RfDs obtain from EPA.32b Standard of hexavalent chromium.c Standard of inorganic arsenic.d Data from European Food Safety Authority.50e Standard of mercuric chloride (and other mercury salts).f HI (average exposure level) = ∑THQs; HI (high exposure level) = ∑THQs; CRIt = ∑CRIt. | ||||||
Cr | 3a,b | 0.0071 | 0.0024 | 0.19 | 0.064 | 3.57 (0.49–95.99) |
Ni | 20a | 0.0076 | 0.0004 | 0.31 | 0.016 | |
Cu | 40a | 0.11 | 0.0027 | 0.38 | 0.0096 | |
Zn | 300a | 3.15 | 0.011 | 20.30 | 0.068 | |
As | 0.3a,c | 0.021 | 0.069 | 0.15 | 0.51 | 31.04 (0.89–231.08) |
Cd | 1a | 0.0005 | 0.0005 | 0.0036 | 0.0036 | 0.189 (0.075–1.35) |
Pb | 1.5d | 0.013 | 0.0089 | 0.27 | 0.18 | |
Hg | 0.3a,e | 0.031 | 0.10 | 0.33 | 1.08 | |
HIf/CRIt | 0.20 | 1.94 | 34.79 (1.46–232.62) |
There are significant differences in the contribution rates of the eight metal(loid)s for HI at average exposure levels. Among the heavy metal elements, the contribution rate of Cu is the highest (27.78%), followed by Zn (15.51%), As (13.43%), Cd (13.01%) and Hg (9.62%), while that of Pb, Cr and Ni are quite low (all below 5.00%). While Cu and Zn are essential elements for the human body, their excessive accumulation would be detrimental for human health. The EDIs at the average exposure levels of Cu and Zn are much lower than the RfD values, and the THQs are below 1.0, implying that Cu and Zn are not high-risk elements. Although THQs of As, Cd and Hg are below 1.0, these toxic elements could still cause serious health issues to the general public.
For the single element, the average carcinogenic risk indexes of Cr, As, and Cd are all lower than 10−4 (Table 5), indicating that the carcinogenic risk of the residual metal(loid)s in the studied fish are acceptable. The total carcinogenic risk index ranges from a minimum of 1.46 × 10−6 to a maximum of 232.62 × 10−6 (an average value of 34.79 × 10−6) in fish consumption in Northeast China. The results show the potential carcinogenic risk of fish consumption in Northeast China. The levels of carcinogenic elements (Cr, As, and Cd) in fish in this area should be monitored.
This journal is © The Royal Society of Chemistry 2019 |