Mutagenesis assays on urines produced by patients administered adriamycin and cyclophosphamide.

The XAD-2 resin concentration/elution system for concentration of mutagens contained in urines was optimized for cancer patients who had been administered such antineoplastic agents as adriamycin (ADR; doxorubicin), cyclophosphamide (CP), methotrexate, vincristine, and 5-fluorouracil. In the reverse mutation assay, Salmonella typhimurium strains TA1535 and TA98 differentiated between CP (with S9 fraction) and ADR (without S9), respectively. No dose-response for CP was observed. There was a dose-response to ADR by TM677 in the presence of S9 using a forward mutation assay. However, while the reverse mutation assays successfully detected ADR and CP administration in the presence of each other in terms of urine mutagenicity, the forward mutation assay did not, since unidentified CP metabolites were also detected in the latter. None of these systems detected mutagenic urines from tobacco smokers, although reaction of these urines with beta-glucuronidase allowed this type of source to be detected also.

Non-mutagenicity for Salmonella of the chlorinated hydrocarbons aroclor 1254, 1,2,4-trichlorobenzene, mirex and kepone.

A polychlorinated biphenyl mixture, Aroclor 1254, two commercial grade insecticides, mirex and kepone, and a pesticide breakdown product, 1,2,4-trichlorobenzene were evaluated for mutagenicity and hepatic enzyme induction potential in the Salmonella/microsomal assay. None was found to revert strains TA1535, TA1537, TA98 or TA100 when tested with or without metabolic activation. Liver microsomal extracts (S9) from rats induced with 1,2,4-trichlorobenzene were shown to differ from S9 of either control or Aroclor 1254-induced rats in the capacity to activate 2-aminoanthracene mutagenesis.

Evaluating comparative potencies: developing approaches to risk assessment of chemical mixtures.

The U.S. EPA must provide guidance as to health risk assessment of mixtures from a variety of sources such as wastewaters, hazardous waste sites and air particulates. One approach to risk assessment of mixtures is to add up risk assessments for individual components identified as part of the mixture, after considering the potential for interaction among those components. This provides an index of hazard potential but not a quantitative estimate. When data on mixture components are incomplete, but these components are isomers or congeners of a well-studied chemical, another technique--use of toxic equivalency factors--can be applied. This approach has been proposed for estimating risk associated with chlorinated dioxins and dibenzofurans. A third approach, that of relative or comparative potency, is based on the assumption that for similar but not necessarily definable complex mixtures, a measure of relative potency based on data from in vitro tests can be correlated in a constant fashion with relative potency from an in vivo bioassay. The degree of confidence in the appropriateness of a relative potency method rests upon the way potency is measured and the validity of underlying assumptions (the degree to which these assumptions can be tested). One class of assumptions involves choice of the model or procedure for deriving the quantitative risk estimates. A second set of assumptions deals with mechanism of action, and whether such considerations add bias or, in fact, refine the relative potency judgment. The choice of short-term tests appropriate for use in establishing the potency relationships is also a factor to be considered. This paper presents examples of proposed uses of relative potency in risk assessment and outlines some areas for further study.

Biological considerations for combining carcinogenicity data for quantitative risk assessment.

Quantitative risk assessments for carcinogens conducted by the U.S. EPA have most frequently been based on results of a bioassay from a single sex/strain/species of animal. In some cases, more than one data set derived from different sexes, strains, or species of animals is suitable for quantitative risk assessment. When there is no apparent difference among the data sets in sensitivity to the carcinogen, use of more of the available data should result in a higher level of confidence in the risk estimate. Several biological factors must be considered before combining data from different animal sexes, strains, species, or tumor sites. The relevance of the animal models, study design and execution, dose selection, and route of administration are factors which influence whether data from separate studies should be combined. The decision to combine data sets is also based on what is known of the mechanism of action of the agent, its pharmacokinetics, any species/sex specificity of the effect, and considerations regarding tumor site specificity. Statistical analysis also indicates whether the data sets may be described by the same multistage model. The evaluation of these factors in the decision to combine or not combine data sets is discussed.

A statistical test of compatibility of data sets to a common dose-response model.

Quantitative estimates of cancer risk generally involve low-dose extrapolation based on an exponential dose-response model for dichotomous response data. Frequently more than one data set is available. If a careful analysis of the biological issues indicates that more than one of the available data sets could be used in the quantitative estimate of cancer risk, it is reasonable to think of combining the data. Before combining data, however, it would be prudent to test whether the data sets are compatible with a common dose-response model. If they are not, it could be concluded that an underlying biological factor is responsible. If they are statistically compatible, the decision to combine data sets based on biological issues would be reinforced. A statistical test based on the generalized likelihood ratio method is proposed for evaluating the compatibility of different data sets with a common dose-response model. This method of constructing a statistical test and the associated asymptotic theory is consistent with the approach used by GLOBAL86 (R. B. Howe, K. S. Crump, and C. Van Landingham, GLOBAL86: A Computer Program to Extrapolate Quantal Animal Toxicity Data to Low Doses, K. S. Crump & Co., Ruston, LA, 1986) for estimating the confidence limits that are used as a basis for quantitative estimates.

Mutagenic studies of folic acid antagonists.

Compounds that compete with folic acid (folic acid antagonists [FAAs]) become limited in their usefulness in the treatment of leukemia, malaria, and bacterial infections by the rapid development of resistance. Assays of the plasma levels of certain of these FAAs led to the observation, in about 25% of the determinations, that a higher density of growth of Streptococcus faecium var. durans (ATCC 8043) was obtained at an FAA concentration just below the completely inhibitory level than at one-half this concentration. This and other considerations suggested that FAAs may act not only as selective agents for resistant organisms but also as mutagens. Seven FAAs including amethopterin, pyrimethamine, trimethoprim, chlorguanide triazine, an experimental quinazoline, WR-158,122, and two experimental triazines, WR-99,210 and WR-38,839, were tested for mutagenicity in the Salmonella reversion assay developed by Ames et al. (1975). All were found to be negative for strains TA1535, TA1537, TA1538, TA98, and TA100, both with and without microsomal activation. These compounds were then tested as mutagens for three traits in the folic acid-requiring S. faecium. FAAs were shown to cause mutations to folic acid independence, rifampin resistance, and FAA resistance. It is postulated that the FAAs induce mutations by causing thymine deprivation in the folic acid-requiring host.

Urinary biological monitoring markers of anticancer drug exposure in oncology nurses.

People handling anticancer drugs or their wastes may absorb these potent genotoxic agents. The aim of this study was to determine the utility of some general urinary markers among 24 female oncology nurses handling these drugs in comparison with 25 "unexposed" nurses. The markers were the Salmonella typhimurium reverse and forward mutation assays, total thioethers, and D-glucaric acid. The reverse mutation assay was the most specific and sensitive marker for anti-cancer drug exposure. Use of the marker battery was no great advantage as a screening tool relative to use of the reverse mutation assay alone. Better recording of work practices in nurse work logs would have improved interpretation of results.

Combination of cancer data in quantitative risk assessments: case study using bromodichloromethane.

There are often several data sets that may be used in developing a quantitative risk estimate for a carcinogen. These estimates are usually based, however, on the dose-response data for tumor incidences from a single sex/strain/species of animal. When appropriate, the use of more data should result in a higher level of confidence in the risk estimate. The decision to use more than one data set (e.g., representing different animal sexes, strains, species, or tumor sites) can be made following biological and statistical analyses of the compatibility of the these data sets. Biological analysis involves consideration of factors such as the relevance of the animal models, study design and execution, dose selection and route of administration, the mechanism of action of the agent, its pharmacokinetics, any species- and/or sex-specific effects, and tumor site specificity. If the biological analysis does not prohibit combining data sets, statistical compatibility of the data sets is then investigated. A generalized likelihood ratio test is proposed for determining the compatibility of different data sets with respect to a common dose-response model, such as the linearized multistage model. The biological and statistical factors influencing the decision to combine data sets are described, followed by a case study of bromodichloromethane.

Residue organic mixtures from drinking water show in vitro mutagenic and transforming activity.

Indications of possible health effects of residue organics in drinking water have been sought using short-term tests of mutagenic and transforming activity. Ten percent or less of the total organic material in drinking water has been identified; the remainder is believed to include thousands of unknown nonvolatile compounds. Residual organics were concentrated from drinking water from representative U.S. cities by reverse osmosis followed by liquid-liquid extraction [yielding the reverse osmosis concentrate-organic extract (ROC-OE) fraction] and sorption-desorption on XAD-2 resin. Samples of these residue organics were provided by the Environmental Protection Agency for bioassay. They were examined for mutagenic activity by using Salmonella tester strains (primarily TA98 and TA100) and for transforming activity by using mouse fibroblasts (BALB/3T3 clone 1-13). City-specific patterns of dose-dependent bacterial mutagenesis and of bacterial toxicity were observed for these samples and for subfractions generated by sequential extractions with hexane, ethyl ether, and acetone. Mutagenic effects were essentially independent of a microsome activation system prepared from liver of Aroclor 1254-induced rats. On the basis of strain-specific effects in mutagenesis and differential distributions of mutagenic activity during liquid-liquid extraction, at least some of the active compounds are thought to be acidic, frameshift mutagens. The ROC-OE fraction of a New Orleans sample transformed BALB/3T3 cells in replicate experiments. By comparison with the bacterial mutagenesis data, cell transformation is a relatively sensitive method for detecting possible mutagenic and carcinogenic activity in this sample. The appropriateness of these systems for the assay of complex mixtures and the degree to which reverse osmosis concentrates contain the unaltered organic compounds in the original samples are discussed.