巢湖表层沉积物重金属的分布特征及生物有效性
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摘要
为分析沉积物中重金属的分布特征、相互关系及其可能来源,以安徽巢湖表层沉积物为研究对象,利用原子吸收分光光度法(AAS)测定5种重金属(铅、铜、镍、锌、镉)总量和同步浸提重金属(SEM)含量,同时测定酸可挥发性硫化物、总氮、总磷、总有机碳等多种指标,利用低影响程度(ER-L)和中影响程度(ER-M)基准值,[∑SEM]/[AVS]模型和[∑SEM]-[AVS]模型,判断预测表层沉积物中重金属的生物有效性。结果显示:重金属总量在全湖的空间分布不均匀,具有入湖口大于湖心的特征,共8个指标超过ER-L基准值,西湖区各金属总量大于东湖区,两者之间具有显著性差异(P<0.05),全湖[∑SEM]/[AVS]的值在1.097～2.076之间,但[∑SEM]-[AVS]的变化范围为0.127～0.996μmol/g;表明重金属Cu、Cd污染较严重,人为输入影响大,AVS对重金属的束缚作用有重要影响,大部分表层沉积物中的重金属生物有效性低。
In order to analyze the distribution characteristics,relationships and the possible sources of heavy metals(HMs) in sediments,total amount of five kinds of HMs(lead,copper,nickel,zinc and cadmium) and its simultaneously extracted metals(SEM) in the surface sediments of Chaohu lake were measured by atomic absorption spectrophotometer(AAS).The acid volatile sulfide(AVS),total nitrogen,total phosphorus,organic carbon were also determinated.Basic value of effects range-low(ER-L) and effects range-median(ER-M),/ model and- model were used to predict the bioavailability of HMs in surface sediments.The results showed that spatial distribution about the total concentration of HMs in sediments was uneven,that were characterized by stream outlet >the lake center,and eight indices were more than ER-L benchmark.The total amount of HMs in the western zones of lake was higher than the eastern zones of lake,and the relationship between two zones of the lake was significant difference(P<0.05).The range of [∑SEM/AVS] was from 1.097 to 2.076,but - varied between 0.127 μmol/g and 0.996 μmol/g.The results suggested that the pollution of Cu and Cd was serious,and anthropogenic inputs were more influencing factor.AVS played an important role in binding the HMs,and the bioavailability of most HMs in sediments was low.
In order to analyze the distribution characteristics,relationships and the possible sources of heavy metals(HMs) in sediments,total amount of five kinds of HMs(lead,copper,nickel,zinc and cadmium) and its simultaneously extracted metals(SEM) in the surface sediments of Chaohu lake were measured by atomic absorption spectrophotometer(AAS).The acid volatile sulfide(AVS),total nitrogen,total phosphorus,organic carbon were also determinated.Basic value of effects range-low(ER-L) and effects range-median(ER-M),/ model and- model were used to predict the bioavailability of HMs in surface sediments.The results showed that spatial distribution about the total concentration of HMs in sediments was uneven,that were characterized by stream outlet >the lake center,and eight indices were more than ER-L benchmark.The total amount of HMs in the western zones of lake was higher than the eastern zones of lake,and the relationship between two zones of the lake was significant difference(P<0.05).The range of [∑SEM/AVS] was from 1.097 to 2.076,but - varied between 0.127 μmol/g and 0.996 μmol/g.The results suggested that the pollution of Cu and Cd was serious,and anthropogenic inputs were more influencing factor.AVS played an important role in binding the HMs,and the bioavailability of most HMs in sediments was low.
引文
[1]杨丽原,沈吉,刘恩峰,等.南四湖现代沉积物中营养元素分布特征[J].湖泊科学,2007,19(4):390-396.
[2]Allen H E,Fu G M,Deng B L.Analysis of acid volatile sulfide(AVS)and simultaneously extracted metals(SEM)for theestimation of potential toxicity in aquatic sediment[J].Environmental Toxicology and Chemistry,1993,12(8):1441-1453.
[3]Lin Y H,Guo M X,Zhuang Y.Determination of acid volatile sulfide and simultaneously extracted metals in sediment[J].Acta Scientiae Circumstantia,1997,17(3):353-358.
[4]Yu K C,Tsai L J,Chen S H,et al.Chemical binding of heavy metals in anoxic river sediments[J].Wat.Res.,2001,35(17):4086-4094.
[5]鲁如坤.土壤农业化学分析[M].北京:中国农业科技出版社,2000.
[6]Glenn A U,Lee R K,Suflita J M.A rapid and simple method for estimating sulfate reduction activity and quantifyinginorganic sulfides[J].Appl.Environ.Microbiol.,1997,63(4):1627-1630.
[7]袁旭音,陈骏陶,于祥.太湖北部底泥中氮、磷的空间变化和环境意义[J].地球化学,2002,31(4):321-328.
[8]李国莲,刘桂建,姜萌萌,等.巢湖表层沉积物与上覆水体中重金属分配特征及其相关性研究[J].中国科学技术大学学报,2011,41(1):9-15.
[9]Long,E R,Morgan,L G.The potential for biological effects of sediments-sorbed contaminants tested in the national statusand trends program[M].Seattle,Washington:NOAA Technical Memowandam,NOS OMA 52,1990.
[10]Long E R,Macdonald D D,Smith S L,Calder F D.Incidence of adverse biological effects within ranges of chemical concen-trations in marine and estuarine sediments[J].Environmental Management,1995,19(1):81-97.
[11]Jenne E A.Trace element sorption by sediments and soils:Sites and proccess[M]//Chappell W,Petersen K.Symposium onmolybdenum in the environment.New York:Marcel Dekker,Inc.,1977:425-553.
[12]Leonard E N,Mattson V R,Benoit D A,et al.Seasonal variation of acid volatile sulfide concentration in sediment cores fromthree northeastern Minnesota lakes[J].Hydrobiologia,1993,271(2):87-95.
[13]Ma D Y,Wang J Y,Yan Q L,et al.The effects on chemical activity of divalent toxic metal in sediment-pore water of acid-volatile sulfide[J].Acta Oceanologica Sinica,1997,19(5):83-90.
[14]Burton G J,Nguyen L T,Janssen C.et al.Field validation of sediment zinc toxicity[J].Environmental Toxicology andChemistry,2005,24(3):541-553.
[15]Hansen D J,Berry W J,Boothman W S,et al.Predicting the toxicity of metal-contaminated field sediments using interstitialconcentration of metals and acid-volatile sulfide normalizations[J].Environmental Toxicology and Chemistry,1996,15(12):2080-2094.
[16]刘文新,李向东.深圳湾水域中重金属在不同相间的分布特征[J].环境科学学报,2002,22(3):305-309.
[2]Allen H E,Fu G M,Deng B L.Analysis of acid volatile sulfide(AVS)and simultaneously extracted metals(SEM)for theestimation of potential toxicity in aquatic sediment[J].Environmental Toxicology and Chemistry,1993,12(8):1441-1453.
[3]Lin Y H,Guo M X,Zhuang Y.Determination of acid volatile sulfide and simultaneously extracted metals in sediment[J].Acta Scientiae Circumstantia,1997,17(3):353-358.
[4]Yu K C,Tsai L J,Chen S H,et al.Chemical binding of heavy metals in anoxic river sediments[J].Wat.Res.,2001,35(17):4086-4094.
[5]鲁如坤.土壤农业化学分析[M].北京:中国农业科技出版社,2000.
[6]Glenn A U,Lee R K,Suflita J M.A rapid and simple method for estimating sulfate reduction activity and quantifyinginorganic sulfides[J].Appl.Environ.Microbiol.,1997,63(4):1627-1630.
[7]袁旭音,陈骏陶,于祥.太湖北部底泥中氮、磷的空间变化和环境意义[J].地球化学,2002,31(4):321-328.
[8]李国莲,刘桂建,姜萌萌,等.巢湖表层沉积物与上覆水体中重金属分配特征及其相关性研究[J].中国科学技术大学学报,2011,41(1):9-15.
[9]Long,E R,Morgan,L G.The potential for biological effects of sediments-sorbed contaminants tested in the national statusand trends program[M].Seattle,Washington:NOAA Technical Memowandam,NOS OMA 52,1990.
[10]Long E R,Macdonald D D,Smith S L,Calder F D.Incidence of adverse biological effects within ranges of chemical concen-trations in marine and estuarine sediments[J].Environmental Management,1995,19(1):81-97.
[11]Jenne E A.Trace element sorption by sediments and soils:Sites and proccess[M]//Chappell W,Petersen K.Symposium onmolybdenum in the environment.New York:Marcel Dekker,Inc.,1977:425-553.
[12]Leonard E N,Mattson V R,Benoit D A,et al.Seasonal variation of acid volatile sulfide concentration in sediment cores fromthree northeastern Minnesota lakes[J].Hydrobiologia,1993,271(2):87-95.
[13]Ma D Y,Wang J Y,Yan Q L,et al.The effects on chemical activity of divalent toxic metal in sediment-pore water of acid-volatile sulfide[J].Acta Oceanologica Sinica,1997,19(5):83-90.
[14]Burton G J,Nguyen L T,Janssen C.et al.Field validation of sediment zinc toxicity[J].Environmental Toxicology andChemistry,2005,24(3):541-553.
[15]Hansen D J,Berry W J,Boothman W S,et al.Predicting the toxicity of metal-contaminated field sediments using interstitialconcentration of metals and acid-volatile sulfide normalizations[J].Environmental Toxicology and Chemistry,1996,15(12):2080-2094.
[16]刘文新,李向东.深圳湾水域中重金属在不同相间的分布特征[J].环境科学学报,2002,22(3):305-309.
目录
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