Mercury lake water

Syers, J.K. Iskandar, I.K. Keeney, D.R. Distribution and Background Levels of Mercury in Sediment Cores from Selected Wisconsin Lakes. Water Air Soil Pollut. 1973 2, 105-118. 

Kamman NC, Lorey PM, Driscoll CT, Estabrook R, Major A, Pientka B, Glassford E. 2003. Assessment of mercury in waters, sediments, and biota of New Hampshire and Vermont lakes, USA, sampled using a geographically randomized design. Environ Toxicol Chem 23 1172-1186. 

Andersson P, Borg H, Kaerrhage P. 1995. Mercury in fish muscle in acidified and limed lakes. Water Air Soil Pollut 80 889-892. 

Haines TA, Komov VT, Matey VE, Jagoe CH. 1995. Perch mercury content is related to acidity and color of 26 Russian lakes. Water Air Soil Pollut 85 823-828. 

Miskimmin BM, Rudd JWM, Kelly CA. 1992. Influence of dissolved organic carbon, pH, and microbial respiration rates on mercury methylation and demethylation in lake water. Can J Fish Aquat Sci 49 17-22. 

Meyer MW, Evers DC, Daulton T, Braselton WE. 1995. Common loons (Gavia immer) nesting on low pH lakes in northern Wisconsin have elevated blood mercury content. Water Air Soil Pollut 80 871-880. 

Lake water Siberia, Lake Baikal, summer 1992-93 Total mercury 0.14-0.77 14... 

Anderson, M.R., D.A. Scruton, U.P. Williams, and J.F. Payne. 1995. Mercury in fish in the Smallwood Reservoir, Labrador, twenty one years after impoundment. Water Air Soil Pollut. 80 927-930. Andersson, P., H. Borg, and P. Karrhage. 1995. Mercury in fish muscle in acidified and limed lakes. Water Air Soil Pollut. 80 889-892. 

Driscoll, C.T., V. Blette, C. Yan, C.L. Schofield, R. Munson, and J. Holsapple. 1995. The role of dissolved organic carbon in the chemistry and bioavailability of mercury in remote Adirondack lakes. Water Air Soil Pollut. 80 499-508. 

Lathrop, R.C., P.W. Rasmussen, and D.R. Knauer. 1991. Mercury concentrations in walleyes from Wisconsin (USA) lakes. Water Air Soil Pollut. 56 295-307. 

Stephens, G.R. 1995. Mercury concentrations in fish in a remote Canadian arctic lake. Water Air Soil Pollut. 

Partly because of this concern, the Wisconsin Department of Natural Resources, in cooperation with the Electric Power Research Institute, initiated an extensive study of Hg cycling in seepage lakes of north-central Wisconsin (14). The mercury in temperate lakes (MTL) study used clean sampling and subnanogram analytical techniques for trace metals (10, 17) to quantify Hg in various lake compartments (gaseous phase, dissolved lake water, seston, sediment, and biota) and to estimate major Hg fluxes (atmospheric inputs, volatilization, incorporation into seston, sedimentation, and sediment release) in seven seepage lake systems. 

The distribution of Hg within seepage lakes is a net result of the processes that control Hg transport between the atmosphere, water column, seston, sediments, and groundwater. This discussion focuses on the processes that control the exchange of Hg between the sediments and lake water. We first present data on spatial and temporal concentrations in the water column, sediments, pore water, and groundwater. These data set the context for a subsequent discussion of the chemical and physical processes responsible for the transport of mercury across the sediment-water interface and are necessary for assessing transport rates. 

The rate of methylation of mercury in anaerobically incubated estuarine sediments proved to be inversely related to salinity (267) this is consistent with results reported in Section II,A. Methylmercuric ion forms in sediments upon addition of HgCl2, with a lag phase of 1 month (268). Biomethylation by lake water columns and by sediments coincided, apparently being related to overall microbial activity, and showed periodic fluctuations (269). Topping and Davies have demonstrated that mercury can be methylated in the water column of a sea loch (270). As has previously been noted, tin compounds can be methylated by sediments (121-124), and this is also true for lead (134-136, 271). The relative proportions of biotic and abiotic methylation processes for such systems still remain to be determined. 

Table 5 shows the HMBC of 7 MSW landfill leachates for copper, zinc and mercury. These data indicate that the MSW landfill leachate metal binding capacity was relatively high and was site-specific. HMBCs for the MSW leachate samples ranged from of 2.9 to 114.9, 4.9 to 45.2, and 3.6 to 100.8 for HMBC-Cu+2, HMBC-Zn+2, and HMBC-Hg+2, respectively. Comparatively, much lower HMBC values were obtained for other environmental samples, such as lake water (Lake Alice and Lake Beverly) and a wastewater treatment plant effluent (data not shown). 

Amyot M., Mierle G., Lean D. R. S., and McQueen D. J. (1994) Sunlight-induced formation of dissolved gaseous mercury in lake waters. Environ. Set Technol. 28(13), 2366-2371. 

Vandal G. M., Fitzgerald W. F., and Mason R. P. (1991) Cycling of volatile mercury in temperate lakes. Water Air Soil Pollut. 56, 791-803. 

Kerry A, Welboum PM, Prucha B, et al. 1991. Mercury methylation by sulphate-reducing bacteria from sediments of an acid stressed lake. Water Air Soil Pollut 56 565-575. 

Furutani, A. and J.W.M. Rudd. 1980. Measurement of mercury methylation in lake water and sediment samples. Appl. Environ. Microbiol. 40 770-776. 

Chau, Y.-K. and Saitoh, H. (1970). Determination of submicrogram quantities of mercury in lake waters. Environ. Sci. Techn., 4, 839. 

Nojiri, Y., Otsuki, A. and Fuwa, K. (1986) Determination of sub-nanogram-per-liter levels of mercury in lake water with atmospheric pressure helium microwave induced plasma emission spectrometry. Anal. Chem., 58, 544-547. 

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