, 2011). After PCB use and manufacture was banned in the United States in 1977, direct environmental selleck chemicals exposure of humans decreased (Hu et al., 2011 and Knobeloch et al., 2008). However, exposure via consumption
of fish from contaminated waters remains a concern. Lake Michigan has the highest PCB concentrations of all the Great Lakes (Carlson and Swackhamer, 2006 and Hu et al., 2011). All states bordering Lake Michigan continue to issue consumption advisories for Lake Michigan fish due to PCB concentrations. Furthermore, ten watersheds contributing to Lake Michigan have been identified as sources of PCBs requiring remediation (Great Lakes Commission, 2002). While CDK inhibitors in clinical trials PCB concentrations in lake fishes dropped markedly following restrictions on PCBs’ manufacture, use, and disposal, recent trends display more moderate declines (Bhavsar et al., 2007, Chang et al., 2012, Hickey et al., 2006 and Hu et al., 2011). Modeling trends
of PCBs in Lake Michigan fish are a potential way to evaluate efforts to remediate ongoing sources of PCBs to Lake Michigan in light of other factors that also affect PCB concentrations in fish (i.e. gender, age/size, diet, lipids or condition; de Boer et al., 2010, French et al., 2006, Gewurtz et al., 2011, Jude et al., 2010, Madenjian et al., 2010 and Sadraddini et al., 2011). In the 1970s, the Wisconsin Department of Natural Resources (WI DNR) began widespread
testing of many fish species including Lake Michigan chinook and coho for DDT, PCBs, and other chlorinated chemicals. In this paper we examine the form of temporal trends in PCB concentrations in Lake Michigan chinook and coho salmon filets collected over the period 1975–2010, and compute trend estimates while accounting for other predictor variables that may affect the concentrations. Olopatadine Collections were mostly conducted during fall migration at weirs using nets or by electrofishing using standard fisheries practices (Bonar et al., 2009). Salmon were also collected from open waters using gill nets as a part of fisheries assessments or through angler donation programs (typically in warmer months). Annual collections occurred from 1975 to 1990, after which biennial sampling was instituted. After collection, individual fish were measured for length, labeled, frozen and transported to the Wisconsin State Laboratory of Hygiene (WSLH) where they were weighed and fileted. Fish age was estimated for a subset of fish using scales or based on marking and stocking information. Gender of a subset was determined by gross visual examination of gonads. Skin-on filets were homogenized using a meat grinder and subsamples placed in glass jars with foil under the lid and frozen at − 20 °C until analysis. Lipid content of homogenates was determined gravimetrically (Schmidt, 1997).