Finfish

Animal aquaculture is concentrated on finfish, moUuscs, and cmstaceans. Sponges, echinoderms, tunicates, turtles, frogs, and alligators are being cultured, but production is insignificant in comparison with the three principal groups. Common and scientific names of many of the species of the finfish, moUuscs, and cmstaceans currently under culture are presented in Table 2. Included are examples of bait, recreational, and food animals. 

In a similar way, microalgal biomass on the sediment surface can be estimated by measuring the chlorophyll contents in benthic microalgae, which are single-celled microscopic plants that inhabit the top 0 to 3 cm of a sediment surface and are sometimes referred to as microphytobenthos. These organisms are the primary food resources of benthic grazers such as shellfish and numerous finfish species. 

Prey fish are here defined as small, usually short-lived, finfish. In North American fresh waters, many are members of the cyprinid (minnow), percid (perch), and centrarchid (sunfish) families. Prey fish are widely distributed, common, and important in the transfer of MeHg to higher trophic levels, such as piscivorous fish and many fish-eating birds. MeHg concentrations in prey fish of uniform age are less... 

Eustace, I.J. 1974. Zinc, cadmium, copper, and manganese in species of finfish and shellfish caught in the Derwent Estuary, Tasmania. Austral. Jour. Mar. Freshwater Res. 25 209-220. 

Greig, R. and D. Wenzloff. 1977. Final report on heavy metals in small pelagic finfish, euphausid crustaceans and apex predators, including sharks, as well as on heavy metals and hydrocarbons (C 15+) in sediments collected at stations in and near deepwater dumpsite 106. Vol. III. Contaminant inputs and chemical characteristics. Pages 547-564 in U.S. Dep. Com. NOAA, Rockville, MD, Baseline Report of the Environmental Conditions on Deepwater Dumpsite 106. 

Mathews, T.D. 1994. Contaminants in recreationally important estuarine finfish from South Carolina. Bull. 

Greig, R.A. and D.R. Wenzloff. 1977. Trace metals in finfish from the New York Bight and Long Island Sound. Mar. Pollut. Bull. 8 198-200. 

Eisenberg, M. and J.J. Topping. 1985. Organochlorine residues in finfish from Maryland waters 1976-1980. Jour. Environ. Sci. Health Part B. Pestic. Food Contam. Agric. Wastes 20 729-742. 

Kennish, M.J. and B.E. Ruppel. 1997. Chlordane contamination in selected freshwater finfish of New Jersey. Bull. Environ. Contam. Toxicol. 58 142-149. 

Hellou, J. 1996. Polycyclic aromatic hydrocarbons in marine mammals, finfish, and molluscs. Pages 229-250 in W.N. Beyer, G.H. Heinz, and A.W. Redmon-Norwood (eds.). Environmental Contaminants in Wildlife Interpreting Tissue Concentrations. CRC Press, Boca Raton, FL. 

Roundnose flounder, Eopsetta grigorjewi Muscle Finfishes 20.1 FW 22... 

Finfish, Netherlands, 1977-1984 Muscle, 4 species Finfish, North America (2.8-10.9) FW 8... 

In Hong Kong, limited to <6 mg As+3/kg FW for edible tissues of finfish and <10 mg As +3/kg for molluscs and crustaceans (Phillips etal. 1982 Edmonds and Francesconi 1993) in Yugoslavia, these values are 2 for fish and 4 for molluscs and crustaceans (Ozretic etal. 1990) in Australia, <1 mg inorganic As/kg FW and in New Zealand <2 mg inorganic As/kg FW — there is no limit on organoarsenicals (Edmonds and Francesconi 1993). In the UK, seafood products should contain <1 mg As/kg FW contributed as a result of contamination (Edmonds and Francesconi 1993)... 

Windom, H., R. Stickney, R. Smith, D. White, and F. Taylor. 1973. Arsenic, cadmium, copper, mercury, and zinc in some species of North Atlantic finfish. Jour. Fish. Res. Board Canada 30 275-279. 

Cancellieri PJ, Burkholder JM, Deamer-Melia NJ, Glasgow HB (2001) Chemosensory attraction of zoospores of the estuarine dinoflagellates, Pflesteria piscicida and P. shumwayae, to finfish mucus and excreta. J Exp Mar Biol Ecol 264 29 15 Carde RT, Millar JG (2004) Advances in Insect Chemical Ecology. Cambridge University Press, New York... 

Carver RA, Griffith FD. 1979. Determination of Kepone (chlordecone) dechlorination products in finfish, oysters, and crustaceans. J Agric Food Chem 27(5) 1035-1037. 

P. Scherpenisse and A.A. Bergwerft, Determination of residues of malachite green in finfish by liquid chromatography tandem mass spectrometry. Anal. Chim. Acta, 529 (2005) 173-177. 

In cases where the depuration of HOCs from BMOs involves enzyme-mediated biotransformations (Eq. 7.4) or active transport mechanisms, and environmental concentrations are high (e.g. near a point source), depuration rates have been shown to follow Michaelis-Menten kinetics (Spade and Hamelink, 1985). Michaelis-Menten kinetics is elicited when an enzyme or active transport system is saturated with a chemical. This type of kinetics is characterized by lower values of keS at sites with high HOC concentrations. If k s are unchanged at high concentration sites, Michaelis-Menten kinetics will result in elevated BAFs. However, if chemical concentrations become toxic, finfish likely avoid the area and sessile organisms such as mussels may close their valves for extended periods (Huckins et al., 2004). 

Using PCB levels in five species of freshwater finfish, collected over a course of 20 years. Stow (1995) failed to find a significant relationship between residue concentrations and percent lipid. The finding of Randall et al. (1991) may explain part of the problem. They found that using different extraction solvents for tissues, lipid concentrations can vary by 3.5 fold and that laboratories vary widely in the type of solvents used for the extraction of HOC residues in tissues. Whole body lipid levels across BMO species typically vary from about 1 to 15% (based on wet tissue weights). Thus, the lipid mediated differences in BMO tissue concentrations may be as high as 15 fold. Unlike BMOs, Standard SPMDs have a uniform lipid content, which precludes any need for lipid normalization, and the extraction or dialysis solvent is standardized. 

Connell (1990) also proposed that, irrespective of whether food or water is the primary source of accumulated chemical, BMP values are near unity in aquatic food chains when differences in lipid content are taken into account. More recently, there has been a general acceptance that even after taking differences in lipid contents into account, BMPs > 1 do occur in some aqnatic food chains (Macdonald, et al., 2002). Typically, BMP% in finfishes are small (e.g., 3.0-fold) when compared to mammals or birds (e.g., 30-fold) fed similar diets. Finally, until the advent of passive samplers such as the SPMDs, BMP multipliers have been easier to estimate than the dissolved phase exposure concentrations. Knowledge of dissolved phase chemical concentrations is a critical part of nnderstanding how aqueons exposure levels relate to the concentrations of residnes measured in organisms in various trophic levels of aquatic ecosystems. 

The impact of paralytic shellfish toxins on the utilization of shellfish resources is widespread and well recognized. The picture is developing that paralytic shellfish toxins also affect finfish resources. Stated simply, paralytic shellfish toxins cause fish kills. 

Fish Products. As explained earlier, it is unlikely that paralytic shellfish toxins have an impact on the utilization of fish products from the point of view of the suitability of fish as food, except perhaps in cases where whole fish are eaten with little processing. Fish simply are unable to accumulate the toxins in their muscle tissues. But the toxins do appear to have an impact on the marketing of fish products, related to consumer wariness of seafood products in general during red tide and PSP incidents. The media blitz surrounding these incidents often leaves consumers unaware of which particular seafood items to be cautious. Consequently, finfish as well as shellfish products have been avoided during these episodes (25). 

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