Indications for the involvement of a CYP3A-like iso-enzyme in the metabolism of chlorobornane (Toxaphene) congeners in seals from inhibition studies with liver microsomes.

The different isoforms of the cytochrome P450 (CYP) system can metabolise a suite of classes of lipophilic, anthropogenic compounds. The bioaccumulative potential as well as the toxicity of xenobiotics may be significantly altered in the process. To compare the metabolic ability of different wildlife species, it is important to identify the different iso-enzymes of CYP, which are responsible for the metabolism of different classes of compounds. This can be achieved with in vitro incubation assays. In the present study, preparations of hepatic microsomes of a harbour seal (Phoca vitulina) and a grey seal (Halichoerus grypus) demonstrated that the chlorobornane (CHB) congeners CHB-32 and -62 were metabolised enzymatically to their hydroxylated derivatives. These derivatives were partially characterised by their NCI mass-spectra. Inhibition studies were carried out to identify the specific CYP isoform(s) responsible for the metabolism of CHB-32 and -62. Ketoconazole has been shown to inhibit CYP3A enzymes in human and rat studies. In this study, ketoconazole caused concentration-dependent inhibition of metabolism of CHB-32 and -62, reaching 80% at the 1.0 microM treatment level. Ellipticine (1.0 microM), which has been shown to inhibit CYP1A1/2, also inhibited CHB-32 and -62 metabolism in the microsomes of grey seal, but to a much lower degree of less than 10 and 24%, respectively. In the same experiment the metabolism of 4,4'-dichlorobiphenyl was already inhibited 70% by ellipticine treatment at the same concentration. This non-ortho substituted PCB congener can easily attain a planar molecular configuration, and therefore served as a model CYP1A substrate. Inhibition of chlorobornane metabolism was not observed after the addition of goat anti-rat CYP2B antibodies or Aldrin, which is a model CYP2B substrate in rat. Cautious interpretation is advised for results obtained with so-called selective competitive inhibitors. Regardless, these studies indicated for the first time the possible involvement a CYP3A isoform in the mediation of chlorobornane metabolism in seals. The immunochemical cross-reactivity of mouse, rabbit or sheep anti-rat antibodies in the hepatic microsomes of harbour seal confirmed the presence of CYP1A1/2, CYP1A1, CYP2B1/2, CYP3A and CYP4A isoenzymes. Enantioselective metabolism by the microsomes of harbour seal was observed for both CHB-32 and -62. Stereochemical preferences of biotransformation enzymes can have an influence on the environmental distribution of both enantiomers of optically active compounds.

Enantiomer fractions instead of enantiomer ratios.

The use of enantiomer ratios (ERs) to indicate the relative amounts of a pair of enantiomers in a sample has some disadvantages. Enantiomer fractions (EFs) are proposed as an alternative expression to eliminate the difficulties.

Toxaphene: a challenging analytical problem.

The analysis of toxaphene, a highly complex mixture of chlorinated bornanes, bornenes and camphenes, is a challenging problem, especially as individual congeners are present at trace levels in biota and other relevant samples. The complicated nomenclature of the compounds of interest is briefly discussed. Gas chromatographic techniques are the most important tools in toxaphene analysis because of their high resolution. The main focus of attention is devoted to important steps in the GC-based analytical procedure, such as sample preparation and injection, separation by single-column and multidimensional GC, both heart-cut and comprehensive, and detection by electron capture and, increasingly, MS-based detection/identification. The gradual shift from total toxaphene to individual compound analysis is discussed, and the growing interest in enantiomer-selective separations is highlighted. The problems encountered when selecting appropriate indicator compounds for rapid toxaphene screening are also addressed.

Environmental occurrence, analysis, and toxicology of toxaphene compounds.

Toxaphene production, in quantities similar to those of polychlorinated biphenyls, has resulted in high toxaphene levels in fish from the Great Lakes and in Arctic marine mammals (up to 10 and 16 microg g-1 lipid). Because of the large variabiliity in total toxaphene data, few reliable conclusions can be drawn about trends or geographic differences in toxaphene concentrations. New developments in mass spectrometric detection using either negative chemical ionization or electron impact modes as well as in multidimensional gas chromatography recently have led researchers to suggest congener-specific approaches. Recently, several nomenclature systems have been developed for toxaphene compounds. Although all systems have specific advantages and limitations, it is suggested that an international body such as the International Union of Pure and Applied Chemistry make an attempt to obtain uniformity in the literature. Toxicologic information on individual chlorobornanes is scarce, but some reports have recently appeared. Neurotoxic effects of toxaphene exposure such as those on behavior and learning have been reported. Technical toxaphene and some individual congeners were found to be weakly estrogenic in in vitro test systems; no evidence for endocrine effects in vivo has been reported. In vitro studies show technical toxaphene and toxaphene congeners to be mutagenic. However, in vivo studies have not shown genotoxicity; therefore, a nongenotoxic mechanism is proposed. Nevertheless, toxaphene is believed to present a potential carcinogenic risk to humans. Until now, only Germany has established a legal tolerance level for toxaphene--0.1 mg kg-1 wet weight for fish.

The use of microsomal in vitro assay to study phase I biotransformation of chlorobornanes (Toxaphene) in marine mammals and birds. Possible consequences of biotransformation for bioaccumulation and genotoxicity.

The factors determining the bioaccumulation of lipophilic compounds in wildlife are often poorly understood, partly because it is difficult to do in vivo experiments with animals such as marine mammals and birds. To evaluate the role of phase I biotransformation in the bioaccumulation process of chlorobornanes (toxaphene), this was studied in in vitro assays with hepatic microsomes of animals that could be sampled shortly after death. The capacity of microsomes to metabolise a technical toxaphene mixture decreased in the order Phoca vitulina (harbour seal) >> Lagenorhynchus albirostris (whitebeaked dolphin) approximately equal to Diomedea immutabilis (Laysan albatross) > Physeter macrocephalus (sperm whale). Harbour seal microsomes metabolised the chlorobornane (CHB) congeners CHB-32 and CHB-62; whitebeaked dolphin and Laysan albatross microsomes only metabolised CHB-32. Metabolism of CHB-26 and CHB-50 was never observed. The negative chemical ionisation (NCI-) mass spectra of some of the hydroxylated metabolites were obtained. The number of peaks in the toxaphene residues of wildlife extracts decreased in the order of increasing in-vitro biotransformation capacity. Thus, the results of the in vitro assays and residue analysis were in accordance, although assays with microsomes of more individuals of the same species are required for a more general conclusion at the species level. Finally, the effect of in vitro biotransformation was evaluated in terms of the genotoxic potential using the Mutatox assay. Only technical toxaphene and CHB-32 were genotoxic in the direct assay, whereas the addition of rat S9 fraction or microsomes of harbour seal and albatross decreased the genotoxic response. Thus, organisms with a low ability to metabolise chlorobornanes, such as whales, may be most affected by the carcinogenic properties of toxaphene. A hypothetical reaction which fits the experimental results is discussed. Based on these results it is concluded that in vitro assays with microsomes of wildlife animals which died a natural cause can act as a valuable tool to assess the occurrence and effects of phase I metabolism. Some precautions are discussed, that should be taken to reduce the chance of false negative results.

Determination of tris(4-chlorophenyl)methanol and tris(4-chlorophenyl)methane in fish, marine mammals and sediment.

Tris(4-chlorophenyl)methanol (TCP) and tris(4-chlorophenyl)methane (TCPMe) were determined in aquatic organisms and sediment by a method based on Soxhlet extraction, gel permeation chromatography, fractionation over silica and gas chromatography/mass spectrometry (GC/MS) analysis. TCPMe was identified as the 4-substituted isomer after synthesis of this compound. TCP could be determined by GC/MS with negative chemical ionistation (GC/NCI-MS) with a detection limit of 0.02 g kg(-1) and a recovery of 90%. TCP concentrations in marine mammals from the North Sea and Dutch Wadden Sea ranged from 0.2 to 2 mg kg(-1), and those in marine and freshwater fish samples from 0.005 to 0.4 mg kg(-1) on a lipid wt basis. TCP concentrations in two Rhine delta sediment samples were 1.2 and 3.0 microg kg(-1) dry wt, respectively. TCPMe concentrations, determined by GC/MS with electron impact (GC/EI-MS), were 10-50% of the TCP concentration in all samples analysed.