Validation human toxicity data

Need for Validation with Human Toxicity Data... 

Human toxicity data, especially the median lethal dose, is extrapolated from animals or from accidental poisoning, homicides and suicides. Extrapolations from animal data are educated estimates which consider the differences in species and building in a safety factor. If a lethal dose is 10 mg/kg in a rat and we consider a human to be 10 times more sensitive 1 mg/kg will have another 10-fold safety margin. Animal testing also involves using what may seem as ridiculous doses in order to cover the safety factor. To find a statistically valid effect which occurs once in one million subjects, several million animals would have to be used, which is exhorbitantly... 

FETAX is a rapid test for identifying developmental toxicants. Data may be extrapolated to other species including mammals. FETAX might be used to prioritize hazardous waste samples for further tests which use mammals. Validation studies using compounds with known mammalian and/or human developmental toxicity suggest that the predictive accuracy rate compares favorably with other currently available "in vitro teratogenesis screening... 

Animal Studies Most toxicity data come from controlled and replicated animal studies. The physiology of animal species varies from humans. As one moves farther away from humans in the zoological chain, the meaningfulness of test results is less valid. Generalization to humans becomes difficult. Standard tests and methods for rating toxicity help estimate human effects. Controlled breeding and raising of test species also help improve reliability and comparability of results. 

Comparative Toxicokinetics. In humans, the targets for trichloroethylene toxicity are the liver, kidney, cardiovascular system, and nervous system. Experimental animal studies support this conclusion, although the susceptibilities of some targets, such as the liver, appear to differ between rats and mice. The fact that these two species could exhibit such different effects allows us to question which species is an appropriate model for humans. A similar situation occurred in the cancer studies, where results in rats and mice had different outcomes. The critical issue appears to be differences in metabolism of trichloroethylene across species (Andersen et al. 1980 Buben and O Flaherty 1985 Filser and Bolt 1979 Prout et al. 1985 Stott et al. 1982). Further studies relating the metabolism of humans to those of rats and mice are needed to confirm the basis for differences in species and sex susceptibility to trichloroethylene s toxic effects and in estimating human heath effects from animal data. Development and validation of PBPK models is one approach to interspecies comparisons of data. 

Currently, there are no validated and regulatory accepted in vitro methods for assessing repeated dose toxicity. Numerous in vitro systems have been developed over the last decades and have been discussed and summarized in recent ECVAM reports on repeated dose toxicity testing (Worth and Balls 2002, Prieto et al. 2005, Prieto et al. 2006). Human in vitro data, particularly on kinetics and metabolism, and in vitro test data from well-characterized target organ and target system models on, e.g., mode of action(s)/mechanism(s) of toxicity may be useful in the interpretation of observed repeated dose toxicity. 

It is noteworthy that the styrene reference concentration (RfC) in the Integrated Risk Information System is based on the biomarker-response relationship found in workers (Mutti et al. 1984 EPA 1998). The Environmental Protection Agency (EPA) used the relationship of urinary biomarker to ambient-air concentration of workers to develop an RfC that was adjusted for the difference in exposure time between the workplace and the general population. That is a valid approach because it derives a workplace concentration-toxicity relationship in workers, which can then be adjusted for the general population to account for differences in exposure time and can take uncertainty factors into account. It is different from direct adjustment of the styrene BEI to evaluate human population biomonitoring data on styrene metabolites in urine, which would have the uncertainties described above and in Chapter 5. 

The principle of estimating a therapeutic index prior to clinical trials typically involves determining the no observable adverse effect level (NOAEL) and comparing that to the projected human dose. In providing the estimate, the efficacious dose is typically obtained from in vitro data with human cells or tissues and in vivo preclinical pharmacology studies that involve animal disease models. Not infrequently the species used to estimate the toxic level is different from the species used to estimate an efficacious level. Thus the therapeutic index is not a true ratio as the units (species and/or conditions) are often different. On the other hand, if one were to obtain information relating to toxicity as well as efficacy from studies employing animal models of disease, a direct estimate of therapeutic index could be made provided that appropriate models had been characterized or validated in the relevant species. 

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