Teratogenic effects of polychlorinated dibenzofurans in combination in C57BL/6N mice

In silico prediction of nuclear receptor binding to polychlorinated dibenzofurans and its implication on endocrine disruption in humans and wildlife

Polychlorinated dibenzofurans (PCDFs) are known to cause endocrine disruption in humans and wildlife but the mechanisms underlying this disruption have not been adequately investigated. In this paper, the susceptibility of the endocrine system to disruption by PCDF congeners via nuclear receptor binding was studied using molecular docking simulation. Findings revealed that some PCDF congeners exhibit high probabilities of binding to androgen receptor in its agonistic and antagonistic conformations. In depth molecular docking analysis of the receptor-ligand complexes formed by PCDFs with androgen receptor in its agonistic and antagonistic conformations showed that, these complexes were stabilized by electrostatic, van der Waals, pi-effect and hydrophobic interactions. It was also observed that PCDF molecules mimic the modes of interaction observed in androgen-testosterone and androgen-bicalutamide complexes, utilizing between 65 and 83% of the amino acid residues used by the co-crystallized ligands for binding. This computational study suggests that some PCDF congeners may act as agonists and antagonists of androgen receptor in humans and wildlife via inapproprate binding to the receptor.

Environmental mechanisms of orofacial clefts

Orofacial clefts (OFCs) are among the most common birth defects and impart a significant burden on afflicted individuals and their families. It is increasingly understood that many nonsyndromic OFCs are a consequence of extrinsic factors, genetic susceptibilities, and interactions of the two. Therefore, understanding the environmental mechanisms of OFCs is important in the prevention of future cases. This review examines the molecular mechanisms associated with environmental factors that either protect against or increase the risk of OFCs. We focus on essential metabolic pathways, environmental signaling mechanisms, detoxification pathways, behavioral risk factors, and biological hazards that may disrupt orofacial development.

Relative sensitivities among avian species to individual and mixtures of aryl hydrocarbon receptor-active compounds

Dioxins and dioxin-like compounds (DLCs) are potent toxicants to most vertebrates. Sensitivities to DLCs vary among species. In the present study, the sensitivities of avian species (chicken [Gallus gallus], ring-necked pheasant [Phasianus colchicus], and Japanese quail [Coturnix japonica]) to some polychlorinated dibenzo-p-dioxins and polychlorinated dibenzofurans (PCDD/Fs) were determined by using species-specific, in vitro, transactivation assays based on a luciferase reporter gene under control of species-specific aryl hydrocarbon receptors. In ring-necked pheasant and Japanese quail, 2,3,7,8-tetrachlorodibenzo-p-dioxin (TCDD) was not the most potent inducer of toxic effects. Especially for Japanese quail, the relative potency values of most of 9 PCDD/Fs tested were greater than for TCDD. The rank order of avian species sensitivities to DLCs was chicken > ring-necked pheasant > Japanese quail. Effects of binary mixtures of TCDD, 2,3,7,8-tetrachlorodibenzofuran, and 2,3,4,7,8-pentachlorodibenzofuran were strictly additive. Moreover, we also found that the primary DLCs that were responsible for most of the potency of the DLC mixtures can be deduced by using ordination in a multidimensional space defined by the avian species sensitivities. Overall, the relative potency and the species sensitivities of these chemicals could guide risk assessments to wild species when exposure to mixtures of DLCs in the environment.

Windows of Sensitivity to Toxic Chemicals in the Development of Cleft Palates

Cleft lip and cleft palate are among the most common birth defects worldwide. There is a genetic component to the development of these malformations, as well as evidence that environmental exposures and prescription drug use may exacerbate or even produce these manifestations. Thus, it is important to understand the underlying mechanisms and when these exposures affect development of the growing fetus. The purpose of this investigation was to critically review the available literature related to orofacial cleft formation following chemical exposure and identify specific time frames for windows of sensitivity. Further, an aim was to evaluate the potential for predicting effects in humans based on animal studies. Evidence indicates that chemical causes of cleft palate development are due to dose and timing of exposure, susceptibility of the species (i.e., the genetic makeup), and mechanism of action. Several studies demonstrated that dose is a crucial factor; however, some investigators argued that even more important than dose was timing of exposure. Data show that the window of sensitivity to environmental teratogens in the development of cleft palates is quite narrow and follows closely the window of palatogenesis in the fetus of any given species.

Comparative temporal toxicogenomic analysis of TCDD- and TCDF-mediated hepatic effects in immature female C57BL/6 mice

Temporal analyses were performed on hepatic tissue from immature female C57BL/6 mice in order to compare the gene expression profiles for 2,3,7,8-tetrachlorodibenzo-p-dioxin (TCDD) and 2,3,7,8-tetrachlorodibzofuran (TCDF). Time course studies conducted with a single oral dose of 300 microg/kg TCDF or 30 microg/kg TCDD were used to compare differential gene expression on complementary DNA microarrays containing 13,361 features, representing 8194 genes at 2, 4, 8, 12, 24, 72, 120, and 168 h. One hundred and ninety-five genes were identified as differentially regulated by TCDF, of which 116 genes were in common with TCDD, with 109 exhibiting comparable expression profiles (correlation coefficients > 0.3). In general, TCDF was less effective in eliciting hepatic vacuolization, and differential gene expression compared with TCDD when given at an equipotent dose based on a toxic equivalence factor (TEF) of 0.1 for TCDF, especially 72-h postadministration. For example, the induction of Cyp1a1 messenger RNA by TCDF was less when compared TCDD. Moreover, TCDF induced less severe hepatocyte cytoplasmic vacuolization consistent with lower lipid accumulations which significantly subsided by 120 and 168 h when compared with TCDD. TCDF-elicited responses correlated with their hepatic tissue levels which gradually decreased between 18 and 168 h. Although both compounds elicited comparable gene expression profiles, especially at early time points, the TCDF responses were generally weaker. Collectively, these results suggest that the weaker TCDF responses could be attributed to differences in pharmacokinetics. However, more comprehensive dose-response studies are required at optimal times for each end point of interest in order to investigate the effect of pharmacokinetic differences on relative potencies that are important in establishing TEFs.

Immunomodulatory effects of in vitro exposure to organochlorines on T-cell proliferation in marine mammals and mice

Marine mammals bioaccumulate various environmental contaminants such as organochlorines (OCs), which biomagnify via the food web. While the immunomodulatory effects of individual OCs have been studied, the effects of mixtures are not well understood. The immunomodulatory effects of polychlorinated biphenyl (PCB) 138, 153, 169, and 180 as well as 2,3,7,8-tetrachlorodibenzo-p-dioxin (TCDD) and all possible mixtures were examined in marine mammals and mice. Lymphocyte proliferation was significantly modulated by OCs in all species tested, mostly by non-coplanar PCBs, as shown using regression analyses. Correlation analyses showed significant correlations (interpreted as additive effects) between OCs in mice, killer whales, and Steller sea lions. Nonadditive synergistic and antagonistic interactions between OCs were detected in most of the species tested. Toxic equivalency (TEQ) values used for OC toxicity assessment failed to predict the immunomodulatory effects measured in mice and marine mammals. The commonly used mouse model failed to predict immunomodulatory effects in other species. Clustering data suggested that phylogeny does not predict toxicity of OCs. Overall, our data suggest the presence of species-specific sensitivities to different mixtures, in which OCs interactions may be complex and that may exert their effects through dioxinlike or dioxin-independent pathways. Lastly, lymphocyte proliferation, an important part of adaptive immunity, was significantly modulated in mice and marine mammals, suggesting the possibility of increased susceptibility to diseases. These findings will be useful to better characterize the risk associated with OC exposure and possibly lead to new conservation and management strategies.

Evaluation of the benchmark dose method for dichotomous data: model dependence and model selection

The benchmark dose (BMD) method was evaluated using the USEPA BMD software. Dose-response data on cleft palate and hydronephrosis for a number of related polyhalogenated aromatic compounds were obtained from the literature. According to chi(2) test statistics, each dichotomous USEPA model failed to adequately describe only 1 of 12 cleft palate data sets. For hydronephrosis, the models were discriminated to a higher extent according to global goodness-of-fit. NOAELs for cleft palate corresponded to BMDLs (the approximate lower confidence limit on the BMD) for extra risks in the range of 5% or below. Model dependence of the BMDL estimate was more pronounced at lower levels of benchmark response (BMR). A BMR of 5% (extra risk) is recommended for cleft palate since model differences at this level were limited for all data. In addition, at BMRs of 5-10% the BMDL for all models was little affected by the specified confidence limit size (in the 90-99% range). For BMDL determination a conservative model selection approach was applied. At the suggested level of BMR (5%) this procedure resulted in use of the same model (multistage model) for the cleft palate endpoint in general. Akaike's information criterion (AIC) was considered for comparison between models. Determination of appropriateness of use of such methods in dose-response applications requires further analysis.

Arabidopsis and the Genetic Potential for the Phytoremediation of Toxic Elemental and Organic Pollutants

In a process called phytoremediation, plants can be used to extract, detoxify, and/or sequester toxic pollutants from soil, water, and air. Phytoremediation may become an essential tool in cleaning the environment and reducing human and animal exposure to potential carcinogens and other toxins. Arabidopsis has provided useful information about the genetic, physiological, and biochemical mechanisms behind phytoremediation, and it is an excellent model genetic organism to test foreign gene expression. This review focuses on Arabidopsis studies concerning: 1) the remediation of elemental pollutants; 2) the remediation of organic pollutants; and 3) the phytoremediation genome. Elemental pollutants include heavy metals and metalloids (e.g., mercury, lead, cadmium, arsenic) that are immutable. The general goal of phytoremediation is to extract, detoxify, and hyperaccumulate elemental pollutants in above-ground plant tissues for later harvest. A few dozen Arabidopsis genes and proteins that play direct roles in the remediation of elemental pollutants are discussed. Organic pollutants include toxic chemicals such as benzene, benzo(a)pyrene, polychlorinated biphenyls, trichloroethylene, trinitrotoluene, and dichlorodiphenyltrichloroethane. Phytoremediation of organic pollutants is focused on their complete mineralization to harmless products, however, less is known about the potential of plants to act on complex organic chemicals. A preliminary survey of the Arabidopsis genome suggests that as many as 700 genes encode proteins that have the capacity to act directly on environmental pollutants or could be modified to do so. The potential of the phytoremediation proteome to be used to reduce human exposure to toxic pollutants appears to be enormous and untapped.

Relative potency values derived from hepatic vitamin A reduction in male and female Sprague-Dawley rats following subchronic dietary exposure to individual polychlorinated dibenzo-p-dioxin and dibenzofuran congeners and a mixture thereof

This study investigated the potency of individual polychlorinated dibenzo-p-dioxins (PCDDs) and dibenzofurans (PCDFs) to reduce hepatic vitamin A in the rat. Dose-response relationships were determined following long-term dietary exposure to 2,3,7, 8-tetrachlorodibenzo-p-dioxin (TCDD), 2,3,4,7, 8-pentachlorodibenzofuran, 1,2,3,4,8-pentachlorodibenzofuran, 1,2,3, 7,8-pentachlorodibenzofuran, 1,2,3,6,7,8-hexachlorodibenzofuran, 1,2, 3,7,8-pentachlorodibenzo-p-dioxin, octachlorodibenzo-p-dioxin, octachlorodibenzofuran, or mixtures of some of these congeners. The aim was to estimate vitamin A-related relative potency (REP) values for each congener in relation to that of TCDD and to investigate if these values were in accordance with REP values estimated for the subchronic toxicity observed in the same study. An additional aim was to investigate if the effect on hepatic vitamin A levels was additive compared to the effect of the individual congeners. The obtained results demonstrate that hepatic vitamin A reduction occurs as a consequence of long-term low-level exposure to 2,3,7, 8-substituted but not to non-2,3,7,8-substituted congeners. Female rats were slightly more responsive to this effect as judged from the lower EC50 values for all the congeners in this sex. The vitamin A-related REP values were similar for female and male rats and were in good agreement with the estimated REP values for subchronic toxicity in the same animals. The vitamin A effect of the individual congeners in the mixture tended to be somewhat less than pure additive for male rats and very close to pure additive for female rats. In conclusion, the presented data show that reduction of hepatic vitamin A is a sensitive marker of an altered retinoid homeostasis following long-term low-dose exposure to dioxin-like compounds, which essentially conforms to their assumed additive mechanism of action.

Effects of polychlorinated dibenzofurans, biphenyls, and their mixture with dibenzo-p-dioxins on ovulation in the gonadotropin-primed immature rat: support for the toxic equivalency concept

Previous studies have shown that 2,3,7,8-tetrachlorodibenzo-p-dioxin (TCDD), 1,2,3,7,8-pentachlorodibenzo-p-dioxin (PeCDD), and 1,2,3,4,7, 8-hexachlorodibenzo-p-dioxin (HxCDD), and their equipotent mixture block ovulation, reduce ovarian weight gain and alter preovulatory hormone levels in a similar manner. The objective of the current experiment was to investigate the effect of other structurally related compounds such as chlorinated furans and biphenyls on ovulation and related hormonal endpoints. The gonadotropin-primed immature female rat model was used to study the effect of 2,3,4,7, 8-pentachlorodibenzofuran (PeCDF), 3,3',4,4',5-pentachlorobiphenyl (PeCB), and 2,2',5,5' tetrachlorobiphenyl (TCB) and their mixture with polychlorinated dibenzo-p-dioxins (PCDDs) on ovulation. Rats were dosed on Day 23 of age at 0900 h with individual congeners (PeCDF, PeCB, TCB) or a mixture of five compounds, which included TCDD, PeCDD, HxCDD, in addition to PeCDF and PeCB. Equine choronic gonadotropin (eCG; 5 IU) was injected 24 h later to induce follicular development. Blood and ovaries were harvested, and ovarian weights determined at various times after eCG. Serum concentrations of 17beta-estradiol (E(2)), progesterone (P(4)), luteinizing hormone (LH), and follicle-stimulating hormone (FSH) were determined by radioimmunoassay. At 72 h after injection of eCG, the number of ova shed was measured by irrigating the ova from oviducts. The slopes of the dose-responses for inhibition of ovulation generated by the individual PeCDF, PeCB, and/or their mixture with PCDDs were similar. PeCDF, PeCB, and the mixture increased serum concentrations of E(2) at 72 h after eCG injection, the day of expected ovulation; in contrast, serum P(4) and FSH were decreased at that same time point. Only the high doses of TCDD, PeCDF, and PeCB blocked LH and FSH surges at 58 h after eCG. The ovarian histology revealed that the effects of PeCDF, PeCB, and the mixture were very similar to those of PCDDs, consisting of ova in large preovulatory follicles and a lack of or reduced number of corpora lutea. Parallel dose-responses of the individual congeners (PeCDF and PeCB) and their equipotent mixture with PCDDs support the toxic equivalency (TEQ) concept for the blockage of ovulation. Thus, PCDDs, PCDFs, and PeCBs appear to block ovulation by the same or a very similar mechanism of action.

Breast-feeding exposure of infants to environmental contaminants--a public health risk assessment viewpoint: chlorinated dibenzodioxins and chlorinated dibenzofurans

Exposure of children to chlorinated dibenzodioxins and chlorinated dibenzofurans via breast-feeding has been well-documented in industrialized countries. Recent studies indicate a possible link between development of subtle health effects in children and their exposure to dioxin-like chemicals from maternal milk. Some examples of the effects are lower vitamin K levels, increased thyroxine levels, and mild changes in liver enzymes. The projected daily intakes of chlorinated dibenzodioxins and chlorinated dibenzofurans are compared with minimal risk levels for intermediate duration oral exposure (15-365 days) derived for these chemicals. Public health recommendations for future actions related to infant intake of chlorinated dibenzodioxin- and chlorinated dibenzofuran-contaminated breast milk are also addressed.

Use of toxic equivalency factors for risk assessment for dioxins and related compounds

TCDD is the most toxic member of a class of polyhalogenated aromatic hydrocarbons that are structurally related, have a similar mechanism of action, and cause the same spectrum of responses. Because of the need to assess the risk from complex mixtures of these chemicals, the international community has adopted an interim approach that assigns relative potency factors to this family of chemicals, based on a comparison with the potency of TCDD. Each chemical that fits the criteria for this class is assigned a toxic equivalency factor, TEF, which is some fraction of that of TCDD. The total toxic equivalency of a mixture, TEQ, is the sum of the weighted potency of each compound in the mixture. Although there may be some variability between different responses in the determination of a TEF value for a compound, endpoint-specific TEFs are usually very similar. There may also be some species differences in TEFs. Again, if pharmacokinetic factors are taken into account, they are usually relatively minor. TEFs based on intake values may also exhibit some differences when compared to those based on target tissue concentrations. Using scientific judgment and a broad data base, interim TEF values have been recommended for PCDDs, PCDFs, and dioxin-like PCBs. Using such values, the TEF approach has been successful at predicting the toxicity of real world mixtures. Ongoing studies from our laboratory have validated the approach for synthetic mixtures that approximate congener ratios found in food samples. Whether non-additive interactions occur with nondioxin-like compounds found in environmentally relevant concentrations remain to be determined.

Halogenated aromatic hydrocarbons and toxicity equivalency factors (TEFs) from the public health assessment perspective

The validity of the toxicity equivalency factors (TEFs) approach to predicting toxicity of mixtures was investigated on the basis of the public health risk assessment that had been posted for different groups of halogenated aromatic hydrocarbons. First, the minimal risk levels (MRLs) were derived based on the databases available for chlorinated dibenzo-p-dioxins (CDDs), chlorinated dibenzofurans (CDFs), and polychlorinated biphenyls (PCBs). The MRL values were then converted to 2,3,7,8-tetrachlorinated dibenzo-p-dioxin (TCDD) toxicity equivalents (TEQs) and compared with each other. There was a good correlation between intermediate duration oral MRLs for TCDD and 2,3,4,7,8-pentaCDF when expressed in TEQs (7 pg/kg/day and 15 pg/kg/day). Although the studies that served for derivation of these MRLs used different species (guinea pigs and rats, respectively), the toxicity endpoints (immunological and hepatic for TCDD and hepatic for 2,3,4,7,8-pentaCDF) were comparable. The hepatic effects were measured by the same techniques (blood chemistry and histopathology), ensuring similar sensitivity. However, there was a discrepancy between acute oral MRLs for TCDD and 2,3,4,7,8-pentaCDF when they were expressed in TEQs (20 pg/kg/day and 500 pg/kg/day, respectively). The studies used for MRL derivation involved not only different species (mice and guinea pigs, respectively), the immunotoxicity endpoints were measured by techniques with different sensitivity (serum complement activity versus histopathology), making comparison difficult. Further calculations showed that the TEFs approach may be feasible for individual coplanar congeners of PCBs, but not for a mixture of Aroclors. Correlations presented here support the concept that the TEFs are valid only if specific criteria for their derivation are met (e.g., a broad database of information, consistency across endpoints, additivity for the effects, a common mechanism of action, etc.). In environmental exposure, the total toxicity of halogenated aromatic hydrocarbons is not necessarily the sum of the total individual congener toxicities because individual congeners compete for the same receptor; therefore, nonadditive behavior may occur.

Subchronic effects of 2,3,7,8-TCDD or PCBs on thyroid hormone metabolism: use in risk assessment

Effects of 2,3,7,8-tetrachlorodibenzo-p-dioxin (TCDD), 3,3',4,4',5-pentachlorobiphenyl (PCB 126), or 2,3,3',4,4',5-hexachlorobiphenyl (PCB 156) on thyroid hormone metabolism were studied in 13-week feeding studies in female Sprague-Dawley rats. The diets were supplemented with the compounds tested at concentrations ranging from 0.2 to 20 micrograms/kg diet for TCDD, 7 to 180 micrograms/kg diet for PCB 126, or 1.2 to 12 mg/kg diet for PCB 156, respectively. Significant correlations were found for all three compounds between reductions in plasma total thyroxine (TT4) levels and inductions of the microsomal phase II enzyme UDP-glucuronosyltransferase by using T4 as a substrate (T4UGT). Furthermore, the coinduction of certain phase I and II isozymes, i.c., cytochrome P450 1A1 (CYP1A1) and UGT1A1, by these compounds, clearly suggests the involvement of an Ah receptor-mediated mechanism in the disturbance of thyroid hormone metabolism by these polyhalogenated aromatic compounds. These results provide a mechanistic base for the use of certain effects on thyroid hormone metabolism by polyhalogenated aromatic compounds in risk assessment. By using these effects, potencies of PCB 126 and PCB 156 relative to TCDD ranged from 0.008 to 0.1 for PCB 126, and from 0.00007 to 0.004 for PCB 156, respectively. These values correspond very well with relative potencies of PCB 126 and PCB 156 by using some other well-known Ah receptor-mediated toxic and biochemical parameters.

Polychlorinated biphenyls (PCBs): environmental impact, biochemical and toxic responses, and implications for risk assessment

Commercial polychlorinated biphenyls (PCBs) and environmental extracts contain complex mixtures of congeners that can be unequivocally identified and quantitated. Some PCB mixtures elicit a spectrum of biochemical and toxic responses in humans and laboratory animals and many of these effects resemble those caused by 2,3,7,8-tetrachlorodibenzo-p-dioxin (TCDD) and related halogenated aromatic hydrocarbons, which act through the aryl hydrocarbon (Ah)-receptor signal transduction pathway. Structure-activity relationships developed for PCB congeners and metabolites have demonstrated that several structural classes of compounds exhibit diverse biochemical and toxic responses. Structure-toxicity studies suggest that the coplanar PCBs, namely, 3,3',4,4'-tetrachlorobiphenyl (tetraCB), 3,3',4,4',5-pentaCB, 3,3',4,4',5,5'-hexaCB, and their monoortho analogs are Ah-receptor agonists and contribute significantly to the toxicity of the PCB mixtures. Previous studies with TCDD and structurally related compounds have utilized a toxic equivalency factor (TEF) approach for the hazard and risk assessment of polychlorinated dibenzo-p-dioxin (PCDD) and polychlorinated dibenzofuran (PCDF) congeners in which the TCDD or toxic TEQ = sigma([PCDFi x TEFi]n)+sigma([PCDDi x TEFi]n) equivalent (TEQ) of a mixture is related to the TEFs and concentrations of the individual (i) congeners as indicated in the equation (note: n = the number of congeners). Based on the results of quantitative structure-activity studies, the following TEF values have been estimated by making use of the data available for the coplanar and monoortho coplanar PCBs: 3,3',4,4',5-pentaCB, 0.1; 3,3',4,4',5,5'-hexaCB, 0.05; 3,3',4,4'-tetraCB, 0.01; 2,3,3',4,4'-pentaCB, 0.001; 2,3',4,4',5-pentaCB, 0.0001; 2,3,3',4,4',5-hexaCB, 0.0003; 2,3,3',4,4',5'-hexaCB, 0.0003; 2',3,4,4',5-pentaCB, 0.00005; and 2,3,4,4',5-pentaCB, 0.0002. Application of the TEF approach for the risk assessment of PCBs must be used with considerable caution. Analysis of the results of laboratory animal and wildlife studies suggests that the predictive value of TEQs for PCBs may be both species- and response-dependent because both additive and nonadditive (antagonistic) interactions have been observed with PCB mixtures. In the latter case, the TEF approach would significantly overestimate the toxicity of a PCB mixture. Analysis of the rodent carcinogenicity data for Aroclor 1260 using the TEF approach suggests that this response is primarily Ah-receptor-independent. Thus, risk assessment of PCB mixtures that uses cancer as the endpoint cannot solely utilize a TEF approach and requires more quantitative information on the individual congeners contributing to the tumor-promoter activity of PCB mixtures.

Interactions in developmental toxicology: a literature review and terminology proposal

Developmental toxicologists have investigated the interactive effects from concurrent exposures to a variety of chemical and physical agents, including therapeutic drugs, industrial agents, and some biological organisms or their toxins. Of approximately 160 reports of concurrent exposures reviewed in this paper, about one third report no interactive effects (including additive effects--usually referring to response--as opposed to dose-additivity); another one third report antagonistic effects, and the final third report potentiative or synergistic effects. The quality of the studies is highly variable. Frequently, only small numbers of animals were included, and very few dose levels were evaluated. Maternal toxicity was rarely discussed. Time-effect relationships were examined infrequently. In addition, these studies are also inconsistent in the use of terms to describe interactive effects, and more than 90% of the terms were not in harmony with currently accepted definitions in toxicology. Because interaction studies will continue to be important in the future, this paper proposes uniform usage of terms for additivity and interactions in developmental toxicology: additivity (the combined effect of two or more developmental toxicants approximates the sum of the effects of the agents administered separately); antagonism (the combined effect of two or more agents, one or more of which are present at doses that would be developmentally toxic if given individually, is significantly less than the sum of the effects of the agents administered separately); potentiation (the increased effect of a developmental toxicant by concurrent action of another agent at a dose that is not developmentally toxic); synergism (the combined effect of two or more developmental toxicants is significantly greater than the sum of the effects of each agent administered alone); and, interaction if more precise terminology does not apply.

The toxicokinetics and metabolism of polychlorinated dibenzo-p-dioxins (PCDDs) and dibenzofurans (PCDFs) and their relevance for toxicity

This article reviews the present state of the art regarding the toxicokinetics and metabolism of polychlorinated dibenzo-p-dioxins (PCDDs) and dibenzofurans (PCDFs). The absorption, body distribution, and metabolism can vary greatly between species and also may depend on the congener and dose. In biota, the 2,3,7,8-substituted PCDDs and PCDFs are almost exclusively retained in all tissue types, preferably liver and fat. This selective tissue retention and bioaccumulation are caused by a reduced rate of biotransformation and subsequent elimination of congeners with chlorine substitution at the 2,3,7, and 8 positions. 2,3,7,8-Substituted PCDDs and PCDFs also have the greatest toxic and biological activity and affinity for the cytosolic arylhydrocarbon (Ah)-receptor protein. The parent compound is the causal agent for Ah-receptor-mediated toxic and biological effects, with metabolism and subsequent elimination of 2,3,7,8- substituted congeners representing a detoxification process. Congener-specific affinity of PCDDs and PCDFs for the Ah-receptor, the genetic events following receptor binding, and toxicokinetics are factors that contribute to the relative in vivo potency of an individual PCDD or PCDF in a given species. Limited human data indicate that marked species differences exist in the toxicokinetics of these compounds. Thus, human risk assessment for PCDDs and PCDFs needs to consider species-, congener-, and dose-specific toxicokinetic data. In addition, exposure to complex mixtures, including PCBs, has the potential to alter the toxicokinetics of individual compounds. These alterations in toxicokinetics may be involved in some of the nonadditive toxic or biological effects that are observed after exposure to mixtures of PCDDs or PCDFs with PCBs.

Liver accumulation of 2,3,7,8-tetrachloro-[3H]dibenzofuran in mice: modulation by treatments with polychlorinated biphenyls

The distribution of 2,3,7,8-tetrachloro-[3H]dibenzofuran ([3H]TCDF; 40 micrograms/kg) resembled that earlier reported for 2,3,7,8-tetrachlorodibenzo-p-dioxin, with a strong accumulation in the liver and a selective uptake in the nasal olfactory mucosa of adult and fetal mice. Pretreatments with a series of selected congeners of polychlorinated biphenyls (PCBs), i.e.. I (IUPAC)-77, I-105, I-118, I-126, I-153, I-156, I-169, and a commercial preparation, Aroclor 1254 (25-100 mg/kg body wt. i.p.), were found to modulate the hepatic uptake of [3H]TCDF (24 h post-3H-injection). At a short pretreatment time (4 h), non-ortho-chlorinated congeners decreased the uptake of [3H]TCDF equivalents in the liver (e.g., I-126 = 3,3',4,4',5-pentachlorobiphenyl: 34% of control), while several mono- and di-ortho PCB congeners and Aroclor 1254 increased the hepatic uptake of [3H]TCDF (e.g., I-156 = 2,3,3',4,4',5-hexachlorobiphenyl: 183% of control). At a longer pretreatment time (48 h), both a non-ortho (I-169 = 3,3',4,4',5,5'-hexachlorobiphenyl) and mono-ortho PCB congener(s) (e.g. I-156) markedly increased the hepatic 3H-uptake (190%), a probable effect of an induction of hepatic binding sites for TCDF. Ethoxyresorufin-O-deethylase activities, regarded to mirror the metabolic activity of cytochrome P-450 IA1 (CYP IA1), were strongly and time-dependently induced after I-169, but not after I-156, pretreatment (25 mg/kg). The initial liver concentrations of the two PCB congeners were similar and increased for I-169 but not for I-156 at later time points. In conclusion, the results show a selective uptake of [3H]TCDF in the mouse liver and nasal olfactory mucosa of both dam and fetus. The uptake of [3H]TCDF in the liver is influenced both by dose and pre-exposure with PCBs. The presence of a PCB-sensitive, but CYP IA1-independent, hepatic binding site for TCDF is suggested. Consequently, pharmacokinetic interactions with PCBs complicate the toxicity assessment of TCDF in complex mixtures.

Developmental and reproductive toxicity of dioxins and related compounds: cross-species comparisons

Developmental toxicity to TCDD-like congeners in fish, birds, and mammals, and reproductive toxicity in mammals are reviewed. In fish and bird species, the developmental lesions observed are species dependent, but any given species responds similarly to different TCDD-like congeners. Developmental toxicity in fish resembles "blue sac disease," whereas structural malformations can occur in at least one bird species. In mammals, developmental toxicity includes decreased growth, structural malformations, functional alterations, and prenatal mortality. At relatively low exposure levels, structural malformations are not common in mammalian species. In contrast, functional alterations are the most sensitive signs of developmental toxicity. These include effects on the male reproductive system and male reproductive behavior in rats, and neurobehavioral effects in monkeys. Human infants exposed during the Yusho and Yu-Cheng episodes, and monkeys and mice exposed perinatally to TCDD developed an ectodermal dysplasia syndrome that includes toxicity to the skin and teeth. Toxicity to the central nervous system in monkey and human infants is a potential part of the ectodermal dysplasia syndrome. Decreases in spermatogenesis and the ability to conceive and carry a pregnancy to term are the most sensitive signs of reproductive toxicity in male and female mammals, respectively.

Absence of interactions on hepatic retention and 7-ethoxyresorufin-O-deethylation activity after co-administration of 1,2,3,7,8-pentachlorodibenzo-p-dioxin and 2,4,5,2',4',5'-hexachlorobiphenyl

Interactions between 1,2,3,7,8-pentachlorodibenzo-p-dioxin (PnCDD) and 2,4,5,2',4',5'-hexachlorobiphenyl (HxCB) on hepatic retention of PnCDD and on cytochrome P450 related enzyme activities were studied in male C57BL/6J mice. Animals received 8 nmol PnCDD/kg orally, alone or in combination with 1-416 mumol HxCB/kg. Co-administration of HxCB did not alter the hepatic retention of PnCDD or the 7-ethoxyresorufin-O-deethylation (EROD) activity induced by PnCDD as observed after 1 week. A small antagonistic effect on total cytochrome P450 content and 7-pentoxyresorufin-O-depentylation (PROD) activity was observed at a dose of 8 nmol PnCDD/kg and 1 mumol HxCB/kg. Furthermore, a significant induction of PROD activity by PnCDD was found. This was not expected, since PROD activity is considered to be a specific marker for CYP2b related enzyme activity and this type of cytochrome P450 is not induced by polychlorinated dibenzo-p-dioxins such as PnCDD. It is concluded that, under these short-term experimental conditions, no toxicokinetic basis was found to explain the antagonistic effects on hepatic cytochrome P450 related activities observed in the present study or in other studies.

Factors affecting the toxicity of dioxin-like toxicants: a molecular approach to risk assessment of dioxins

The numerous toxic responses of dioxin-like compounds are mediated by the intracellular Ah (aryl hydrocarbon) receptor. It has been suggested that the regulation of dioxins and similar substances could be placed on a molecular foundation by considering the proportion of Ah-receptor sites occupied by toxicant molecules. The present work has shown that the following formation not yet available would be needed in order to develop this approach: correlation between dioxin exposure and human tissue levels; accurate determination of the association constants for human Ah-receptor with toxicant, and for human receptor-ligand complex with DNA; and knowledge of the intracellular concentrations of both receptor binding sites and DNA binding sites. Furthermore, since not all dioxin-like substances behave identically, this information would need to be gathered for a wide variety of substances.

Limited PCB antagonism of TCDD-induced malformations in mice

C57BL/6N mice used to model induction of cleft palate and kidney malformations in offspring following maternal treatment with TCDD, were dosed on gestation day (gd) 9 with 2,2',4,4',5,5'-hexachlorobiphenyl (HCB) (62.5, 125, 250, 500, 1000 mg/kg) and/or gd 10 with 2,3,7,8-tetrachlorodibenzo-p-dioxin (TCDD) (15 or 18 micrograms/kg) to investigate the potential protective effects of HCB against TCDD-induced teratogenicity. Maternal body weight gain was increased by combinations of 15 micrograms TCDD/kg and 125-500 mg HCB/kg and decreased at doses of 15 micrograms TCDD/kg + 1000 HCB mg/kg. At the doses used in this study, there was no effect of either compound on number of live or dead offspring. Fetal body weight was slightly decreased in all groups dosed with greater than or equal to 250 mg HCB/kg. HCB did not induce cleft palate at a dose of 1000 mg/kg, but did induce increases in hydronephrosis and hydroureter at 500 and 1000 mg/kg. Combinations of HCB and TCDD decreased the incidence of cleft palate induced by TCDD alone, but only at doses of 15 micrograms TCDD/kg combined with 125-500 mg HCB/kg. The antagonism of hydronephrosis (incidence and severity) appeared over a narrower dose range (15 micrograms TCDD/kg + 500 mg HCB/kg). HCB induced increases (3-fold) in ethoxyresorufin-O-deethylase (EROD) activity at doses of 500 and 1000 mg/kg, suggesting that the limited antagonism of TCDD teratogenicity by HCB could be under the control of the Ah-receptor.

A critical review of the developmental toxicity and teratogenicity of 2,3,7,8-tetrachlorodibenzo-p-dioxin: recent advances toward understanding the mechanism

A specific teratogenic response is elicited in the mouse as a result of exposure to 2,3,7,8-tetrachlorodibenzo-p-dioxin (TCDD; dioxin). The characteristic spectrum of structural malformations induced in mice following exposure to TCDD and structurally related congeners is highly reproducible and includes both hydronephrosis and cleft palate. In addition, prenatal exposure to TCDD has been shown to induce thymic hypoplasia. These three abnormalities occur at doses well below those producing maternal or embryo/fetal toxicity and are thus among the most sensitive indicators of dioxin toxicity. In all other laboratory species tested, TCDD causes maternal and embryo/fetal toxicity but does not induce a significant increase in the incidence of structural abnormalities even at toxic dose levels. Developmental toxicity occurs in a similar dose range across species; however, mice are particularly susceptible to development of TCDD-induced terata. Recent experiments using an organ culture were an attempt to address the issue of species and organ differences in sensitivity to TCDD. Human palatal shelves examined in this in vitro system were found to approximate the rat in terms of sensitivity for induction of cleft palate. Investigators have suggested that altered regulation of growth factors and their receptors may involve inappropriate proliferation and differentiation of target cells, ultimately producing TCDD-induced terata. Why the teratogenic effects of TCDD are so highly species and tissue specific, and which animal species most accurately predicts the response of the human embryo/fetus, at the levels of exposure experienced by humans, still remains to be clarified.

Structure-dependent induction of aryl hydrocarbon hydroxylase activity in C57BL/6 mice by 2,3,7,8-tetrachlorodibenzo-p-dioxin and related congeners: mechanistic studies

The time- and dose-dependent induction of murine hepatic microsomal aryl hydrocarbon hydroxylase (AHH) and ethoxyresorufin O-deethylase (EROD) activities by five polychlorinated dibenzo-p-dioxin and dibenzofuran congeners showed that the order of induction potency was 2,3,7,8-tetrachlorodibenzo-p-dioxin (TCDD) greater than 2,3,7,8-tetrachlorodibenzofuran (TCDF) greater than 1,2,3,7,8-pentachlorodibenzo-p-dioxin (PCDD) greater than 1,2,3,7,8-pentachlorodibenzofuran (PCDF) greater than 2,3,7-trichlorodibenzo-p-dioxin (TrCDD). These structure-induction relationships were comparable to the structure-toxicity and competitive structure-receptor binding relationships previously reported for these compounds. However, using the corresponding radiolabeled congeners, the direct binding Kd values for dissociation of the cytosolic receptor-ligand complexes were 9.52, 7.96, 1.27, 3.10, and 8.31 nM for the 2,3,7,8-TCDD, 2,3,7,8-TCDF, 2,3,7-TrCDD, 1,2,3,7,8-PCDD, and 1,2,3,7,8-PCDF congeners and these data were clearly not structure dependent (i.e., similar to the structure-activity relationships). Some of the molecular properties for several radioligand-receptor complexes were similar; for example, the sedimentation coefficients for the cytosolic and nuclear receptor complexes varied from 8.8-10.4 S and 5.98-7.0 S, respectively, and the nuclear receptor complexes for all the radioligands eluted from a DNA-Sepharose column at salt concentrations of 0.27-0.29 M. Treatment of the mice with a maximum inducing dose of 2,3,7,8-[3H]TCDD resulted in a time-dependent formation of the nuclear receptor complex which was maximized between 16-24 hr and subsequently decreased up to 72 hr after initial exposure. In parallel studies, the nuclear receptor complex levels were determined 16 hr after treatment of the mice with different doses (2.25, 4.5, and 45 micrograms/kg) of all five radioligands. The results showed that at submaximal induction of the monooxygenase enzyme activities there was a linear correlation between the induced AHH or EROD activities (after 32 hr) and the corresponding nuclear receptor complex levels. It was also apparent from the data that the relative levels of nuclear receptor complex were structure dependent and this suggests that the transformation or activation of cytosolic receptor complexes may be a ligand structure-dependent process which correlates with the observed structure-activity relationships for 2,3,7,8-TCDD and related compounds.

Relative toxicity and tumor-promoting ability of 2,3,7,8-tetrachlorodibenzo-p-dioxin (TCDD), 2,3,4,7,8-pentachlorodibenzofuran (PCDF), and 1,2,3,4,7,8-hexachlorodibenzofuran (HCDF) in hairless mice

2,3,7,8-Tetrachlorodibenzo-p-dixoin 2,3,4,7,8-pentachlorodibenzofuran (PCDF), and 1,2,3,4,7,8-hexachlorodibenzofuran (HCDF) are highly toxic members of a class of environmental contaminants, the polychlorinated aromatic hydrocarbons (PCAH), which exhibit a similar and highly characteristic spectrum of toxic effects. For purposes of risk assessment, it is important to be able to make accurate estimates of the relative potency of these and related compounds. Previous investigations have indicated that, in acute exposure or in vitro studies, PCDF is approximately 0.1 times as toxic and HCDF is approximately 0.01 times as toxic as TCDD. In this study, we compared the relative toxicity and tumor-promoting abilities of TCDD, PCDF, and HCDF in hairless mouse skin. Female hairless mice (HRS/J hr/hr) were treated dermally with the initiator MNNG, then dosed twice weekly for 20 weeks with acetone, TCDD (2.5-10 ng/mouse/dose), PCDF (25-100 ng/mouse/dose), or HCDF (250-1000 ng/mouse/dose) as promoter. TCDD, PCDF, and HCDF were all potent promoters for the induction of squamous cell papillomas. There was, however, no difference in the incidence or multiplicity of papilloma formation between groups. The same doses of the three PCAH, in the absence of initiator, induced no skin papillomas. TCDD produced a significant increase in liver:body weight ratio (p less than 0.001) at all doses and a decrease in thymus:body weight ratio at a dose of 10 ng (p less than 0.001). Mice treated with PCDF and HCDF had marked thymic and splenic involution, liver hypertrophy, mucous cell hyperplasia in the fundic portion of the glandular stomach, and loss of body weight. PCDF and HCDF produced a greater incidence and severity of dermatotoxic effects than TCDD. Based on data for dermal toxicity and changes in body weight and organ weights, PCDF is estimated to be 0.2 to 0.4 times, and HCDF 0.08 to 0.16 times, as toxic as TCDD following repeated dermal exposure. Therefore, toxic equivalence factors generated using data from acute and/or in vitro studies may underestimate the risk from repeated low-dose exposures to these compounds.

Structure-activity relationships in the developmental toxicity of substituted phenols: in vivo effects

Hansch analysis, a quantitative approach relating the physical-chemical properties of molecules to biological effects, was applied to a series of substituted phenols tested for developmental toxicity. The physical-chemical properties included a hydrophobic parameter (log P), an electronic parameter (Hammett sigma), and a bulk parameter (molar refractivity (MR]. Biological activities (potencies) were obtained for 27 congeners in a Chernoff/Kavlock Assay performed in Sprague-Dawley rats exposed on day 11 of gestation. The potencies discussed in this report are the following: the dose to decrease maternal weight gain by 10 g at 24 and 72 hours after treatment (MTOX1 and MTOX2); the dose to increase postimplantation loss by 1 over the concurrent control value (PLOSS); and the dose required to decrease total litter weight by 10% on postnatal day 6 (BIO6). A quantitative structure-activity relationship QSAR was developed for the maternal data (1/MTOX1 = (0.0344*log P) + (-0.1503*sigma) + 0.1195; n = 22, r = 0.81, P less than .0001), which related increasing lipophilicity and decreasing electron-withdrawing ability of the substituent on 22 para-phenols to increasing toxicity. Another QSAR was developed from eight para-phenols that had the greatest postimplantation loss potencies (i.e., less than 100 mmol/kg). The model (1/PLOSS = (-0.2676*log P) + (-0.1827*sigma) + (0.0265*MR) + 0.4420; n = 8, r = 0.93, P less than .0298) related decreasing lipophilicity and electron-withdrawing ability and increasing bulk properties to the decreased viability of implantation sites. However, no descriptor was identified that distinguished the more potent from the less potent congeners for postimplantation loss, and no QSAR was found for litter weight on postnatal day 6 (even when limiting the analysis to the more potent congeners). Congeners were also grouped on a qualitative level according to whether they induced a biological effect below a dose of 6 mmol/kg (termed active), between 6 and 11 mmol/kg (moderately active), or greater than 11 mmol/kg (inactive). Overall, 14 of 27 congeners were classified as active in terms of maternal effects, but only 50% of these were active for developmental effects. Seven of the nine overall active developmental toxicants were active maternal toxicants. Four of the developmental toxicants produced a syndrome of effects that may be related to a similar mechanism of action or common metabolic pathway. Thus, from both quantitative and qualitative viewpoints, the properties of these phenolic congeners that promote maternal toxicity are different from those that contribute to developmental toxicity. It is therefore likely that the mechanisms of toxicity behind these effects are also different.

Polychlorinated biphenyls (PCBs), dibenzo-p-dioxins (PCDDs), dibenzofurans (PCDFs), and related compounds: environmental and mechanistic considerations which support the development of toxic equivalency factors (TEFs)

Halogenated aromatic compounds, typified by the polychlorinated dibenzo-p-dioxins (PCDDs), dibenzofurans (PCDFs), biphenyls (PCBs), and diphenylethers (PCDEs), are industrial compounds or byproducts which have been widely identified in the environment and in chemical-waste dumpsites. Halogenated aromatics are invariably present in diverse analytes as highly complex mixtures of isomers and congeners and this complicates the hazard and risk assessment of these compounds. Several studies have confirmed the common receptor-mediated mechanism of action of toxic halogenated aromatics and this has resulted in the development of structure-activity relationships for this class of chemicals. The most toxic halogenated aromatic is 2,3,7,8-tetrachlorodibenzo-p-dioxin (TCDD) and based on in vivo and in vitro studies the relative toxicities of individual halogenated aromatics have been determined relative to TCDD (i.e., toxic equivalents). The derived toxic equivalents can be used for hazard and risk assessment of halogenated aromatic mixtures; moreover, for more complex mixtures containing congeners for which no standards are available (e.g., bromo/chloro mixtures), several in vitro or in vivo assays can be utilized for hazard or risk assessment.

Retinoic acid and 2,3,7,8-tetrachlorodibenzo-p-dioxin selectively enhance teratogenesis in C57BL/6N mice

TCDD is one of the most toxic man-made compounds and an extremely potent teratogen in mice. Many of its toxic symptoms resemble those seen during vitamin A deficiency. Vitamin A and its derivatives, such as alltrans-retinoic acid (RA), are also teratogenic in mice, as well as many other species. Both TCDD and RA produce cleft palate in susceptible strains of mice. However, while TCDD produces hydronephrosis, RA does not, and TCDD does not produce limb bud defects while RA does. To determine whether TCDD and RA would enhance or antagonize the teratogenic effects of the other compound, C57BL/6N dams were treated po on Gestation Day (gd) 10 or 12 with 10 ml corn oil/kg containing TCDD (0-18 micrograms/kg), RA (0-200 mg/kg), or combinations of the two chemicals. Dams were killed on gd 18 and toxicity and teratogenicity assessed. Coadministration of TCDD and RA had no effect on maternal or fetal toxicity beyond what would be expected by either compound alone. Cleft palate was induced by RA at lower doses on gd 10 than on gd 12, but by TCDD at lower doses on gd 12 than on gd 10. Sensitivity to TCDD-induced hydronephrosis was similar on both gd 10 and 12. The limb bud defects were only observed when RA was administered on gd 10, not when given on gd 12. No other soft tissue or skeletal malformations were related to administration of TCDD or RA. No effect of TCDD was observed on the incidence or severity of limb bud defects induced by RA, nor did RA influence the incidence or severity of hydronephrosis induced by TCDD. However, the incidence of cleft palate was dramatically enhanced by coadministration of the xenobiotic and vitamin. On both gd 10 and 12, the dose-response curves for cleft palate induction were parallel, suggesting some similarities in mechanism between the two compounds. However, combination treatment resulted in a synergistic response that varied with the stage of development and was tissue specific.

2,2',4,4',5,5'-hexachlorobiphenyl as a 2,3,7,8-tetrachlorodibenzo-p-dioxin antagonist in C57BL/6J mice

At doses as high as 750 to 1000 mumol/kg, 2,2',4,4',5,5'-hexachlorobiphenyl (HCBP) did not cause fetal cleft palate, suppress the splenic plaque-forming cell response to sheep red blood cells, or induce hepatic microsomal ethoxyresorufin O-deethylase (EROD) in C57BL/6J mice. Despite the lack of activity of HCBP in eliciting any of these aryl hydrocarbon (Ah) receptor-mediated responses, competitive binding studies indicated that HCBP competitively displaced 2,3,7,8-[3H]tetrachlorodibenzo-p-dioxin (TCDD) from the murine hepatic cytosolic receptor. Cotreatment of C57BL/6J mice with TCDD (3.7 nmol/kg) and HCBP or 4,4'-diiodo-2,2',5,5'-tetrachlorobiphenyl (I2-TCBP) (400 or 1000 mumol/kg) showed that both compounds partially antagonized TCDD-mediated cleft palate and immunotoxicity (i.e., suppression of the splenic plaque-forming cell response to sheep red blood cells), and HCBP antagonized TCDD-mediated hepatic microsomal EROD induction. Thus, HCBP and I2-TCBP, like the commercial polychlorinated biphenyl mixture Aroclor 1254, were partial antagonists of TCDD action in C57BL/6J mice; however, it was also apparent from the results that Aroclor 1254 was the more effective antagonist at lower doses. Using [3H]TCDD, it was also shown that some of the effects of HCBP on TCDD-mediated cleft palate may be due to the decreased levels of TCDD found in the fetal palates after cotreatment with TCDD and HCBP. 4,4'-[125I2]diiodo-2,2',5,5'-tetrachlorobiphenyl ([125I2]TCBP) of high specific activity (3350 Ci/mmol) was synthesized and used to investigate the direct binding of this compound to the murine hepatic Ah receptor or other cytosolic proteins. No direct specific binding was observed between 125I2-TCBP and any cytosolic proteins using a sucrose density gradient assay procedure. These results contrasted with previous studies with Aroclor 1254 that suggested that this mixture acted as a competitive Ah receptor antagonist.