JSTOR is a not-for-profit service that helps scholars, researchers, and students discover, use, and build upon a wide range of content in a trusted digital archive. We use information technology and tools to increase productivity and facilitate new forms of scholarship. For more information about JSTOR, please contact support@jstor.org.. The National Institute of Environmental Health Sciences (NIEHS) and Brogan & Partners are collaborating with JSTOR to digitize, preserve and extend access to Environmental Health Perspectives. This paper reviews the following problems. sampling, decomposition procedures and most important analytical methods used for selenium determination, e.g., neutron activation analysis, atomic absorption spectrometry, gas-liquid chromatography, spectrophotometry, fluorimetry, and x-ray fluorescence. This review covers the literature mainly from 1975 to 1977.Selenium is widely distributed in the environment (waters, soil, and air) albeit generally in very low concentrations (s, 1 g/g). The selenium content sometimes reaches 0.5 mg/g in limonite rocks, and 2.6 mg/g in vanadium-uranium rocks (1). Data on selenium-containing rocks are from North and South America, USSR and Mediterranean countries (1, 2). Some waters were also reported to contain elevated concentrations of selenium, e.g., Colorado channels or subterranean waters in the region of Orsk.Selenium and its compounds have found broad technological applications, among others in electronics (for production of semiconductors, photocells, and rectifiers), machine industry (for obtaining high-grade steel), glass industry (for staining of glass), chemical industry (as a catalyst), rubber industry (for acceleration of vulcanization), and pharmaceutics (veterinary selenium preparations in treatment of diseases due to selenium deficiency). In agriculture, organoselenium compounds are used as bactericides, fungicides, and herbicides. This broad technological application brings about growing selenium pollution of the atmosphere. For

The concentrations of cadmium, zinc, copper and metallothionein in the autopsy samples of liver among the inhabitants of Lódź (Poland) were determined. The cadmium levels were low in the range of 1.5 to 5.8 micrograms/g. The concentration of metallothionein determined by the Hg-method was high (0.160-1.665 mumol Hg/g); it was mainly a Zn-thionein. The percentage of hepatic zinc bound in the MT-fraction increased with the overall content of zinc in the liver. The elevation of zinc in the liver occurs in the proportion required for the saturation of metal-binding ligands of metallothionein. The role of cadmium remains less clear. Our results suggest that the metallothionein level in the liver increase significantly in response to elevated cadmium concentrations. This response, however, is in high excess to the demand which is justified stoichiometrically.

The levels of Cd, Zn, Cu and metallothionein (MT) were determined in renal cortex and liver of 75 subjects decreased in the period 1986-1989 in the area of Upper Silesia (Katowice). The mean age of the population studied was 53.6 +/- 14.6 years. The determined levels (mean +/- SD) were: 43.1 +/- 23.5 micrograms Cd/g; 52.5 +/- 17.4 micrograms Zn/g; 2.2 +/- 0.7 microgram Cu/g; 0.80 +/- 0.36 mumol Hg/g in renal cortex and 3.5 +/- 2.5 micrograms Cd/g; 82.8 +/- 34.3 micrograms Zn/g; 4.5 +/- 2.6 micrograms Cu/g; 0.69 +/- 0.44 mumol Hg/g in the liver. The level of Cd in renal cortex was 40% higher in smokers compared to nonsmokers and was independent of the gender. Whole-body retention of Cd was 34.1 +/- 18.5 mg; smoking elevated the value from 27.1 to 38.2 mg. Compared with a similar study made in central Poland (Lódź), a significant difference was found only regarding the level of Zn and MT in the liver, pointing to the possibility that exposure to this element in the region of Upper Silesia may be higher.

Cd, Zn, Cu, and metallothionein (MT) levels have been determined in the renal cortex and liver of 70 persons who died in Lodz and its surroundings in the years 1985-1989. The mean concentrations were: 44.9±28.6 µg Cd/g, 52.0±16.7 µg Zn/g, 2.4±1.0 µg Cu/g, 0.79±0.40 µmol Hg/g, and 3.5±1.8 µg Cd/g, 66.7±30.5 µg Zn/g, 4.9±2.1 µg Cu/g, 0.50±0.38 µmol Hg/g wet tissue in renal cortex and liver, respectively, with mean age 54.0±13.8. Smokers showed 2.4 times higher levels of Cd in the renal cortex than non-smokers. The mean body burden of Cd was 33.4±17.3 mg. Smoking increases it twofold from 22.0 mg in non-smokers to 41.8 mg in smokers.

Four groups of rats were given: cadmium chloride (Cd), cadmium chloride and mercuric chloride (Cd + Hg), cadmium chloride and sodium selenite (Cd + Se), or cadmium chloride, mercuric chloride, and sodium selenite (Cd + Hg + Se). All animals received subcutaneous doses of 115mCdCl2 (0.3 mg Cd/kg) every other day for 2 weeks. Mercuric chloride was administered intravenously at doses of 0.5 mg Hg/kg every other day, and Na2 75SeO3 intragastrically at doses of 0.1 mg Se/kg every day for a fortnight. The whole-body and organ retention of cadmium changed slightly with the type of exposure. A significant interaction effect of the examined elements was noted in the nuclear and soluble fractions of the liver and kidneys. Mercury decreased the cadmium concentration in both the nuclear and soluble fractions of the kidneys and diminished the effect of selenium on the cadmium level in the soluble fraction of the kidneys. In the liver the presence of mercury contrary to selenium, lowered the cadmium level in the nuclear fraction. The pattern of cadmium binding to proteins of the soluble fraction of the kidneys and liver remained the same in all groups of animals.