Additive Interactions between Pairs of Polybrominated Dibenzo-p-dioxin, Dibenzofuran, and Biphenyl Congeners in a Rainbow Trout Early Life Stage Mortality Bioassay

Use of fish-specific toxic equivalency factors (TEFs) to estimate the risk that exposure to polybrominated dibenzo-p-dioxins (PBDDs), dibenzofurans (PBDFs), and biphenyls (PBBs) pose to fish early life stage survival depends on validation of the hypothesis that these chemicals act additively to produce mortality. A rainbow trout early life stage bioassay was used to determine how pairs of PBDD, PBDF, and PBB congeners interact to produce 2,3,7,8-tetrachlorodibenzo-p-dioxin (TCDD)-like toxicity associated with sac fry mortality. The congener pairs tested were 2,3,7,8-tetra- bromodibenzo-p-dioxin (2,3,7,8-TBDD)/1,2,3,7,8-pentabromodi- benzop-dioxin (1,2,3,7,8-PBDD); 2,3,7,8-TBDD/1,2,3,7,8-penta- bromodibenzofuran (1,2,3,7,8-PBDF); 1,2,3,7,8-PBDD/2,3,4,7,8-pentabromodibenzofuran (2,3,4,7,8-PBDF); and 2,3,4,7,8-PBDF/3,3′,4,4′-tetrabromobiphenyl (3,3′,4,4′-TBB). Graded doses of each congener alone, or graded doses of fixed ratios of paired congeners were injected into newly fertilized rainbow trout eggs. In all cases, interactions between congener pairs were additive as tested by a probit model. Isobolographic analysis also supported the hypothesis that the PBDD, PBDF, and PBB congeners act additively. Thus, the use of fish-specific TEFs to convert fish tissue concentrations of individual PBDD, PBDF, and PBB congeners to TCDD equivalents (TEs) and then adding the TEs contributed by the various congeners to give the total TCDD equivalents concentration (TEC) in the tissue is supported by these results. By comparing the TEC in feral fish eggs to the fish egg TCDD no-observed-effect level (NOEL) and lowest-observed-effect level (LOEL) for early life stage mortality, the risk that complex mixtures of these polybrominated chemicals in eggs pose to sac fry survival can be estimated.     

Comparative Ability of Various PCBs, PCDFs, and TCDD to Induce Cytochrome P450 1A1 and 1A2 Activity Following 4 Weeks of Treatment

Toxic equivalency factors (TEFs) have been proposed for di benzo-p-dioxins,dibenzofurans, and polyhalogenated biphenyls. The proposed toxicequivalency factors (TEFs), which are presently being evaluatedin our laboratory, are currently used to estimate the potentialhealth risk associated with exposure to complex mixtures containingthese chemicals. In preliminary studies, equally potent doses,based on the published TEEs and relative enzyme-inducing potency,of 2,3,7,8-tetrachioro-dibenzo-p-dioxin (TCDD), 2,3,7,8-tetrachlorodibenzofuran,1,2,3,7,8-pentachlorodibenzofuran, 1,2,3,4,6,7,8,9-octachloro-dibenzofuran,3,4,3',4'-tetrachlorobiphenyl, 2,3,4,3',4'-pentachlo-robiphenyl,3,4,5,3',4'-pentachlorobiphenyl, 2,3,4,3',4',5'-hex-achlorobiphenyl,2,3,4,5,3',4'-hexachlorobiphenyl, and 3,4,5,3',4',5'-hexachlorobiphenylwere administered to female B6C3F1 mice 5 days a week over a4-week period. Hepatic, skin, and lung cytochrome P450 1A1 andhepatic 1A2 activities were determined for all chemicals testedand compared to those from TCDD-treated mice. These initialstudies indicate that the present TEFs do not reliably predictinduction potency for many of the chemicals. Furthermore, ourdata suggest that the relative inductive potency of these chemicalsmay be tissue specific and that estimates of TEFs based on hepaticethoxyresorufin O-de ethylase activity may not accurately reflectthe potency of these chemicals in nonhepatic tissue. The TEFsproposed for the "dioxin-like" polychlorinated biphenyls (PCBs)overestimate the potency of these compounds by factors of 10–1000.The present study indicates that more experimental data arerequired before TEFs for PCBs should be used in regulatory decisionmaking.     

Potency of a Complex Mixture of Polychlorinated Dibenzo-p-dioxin, Dibenzofuran, and Biphenyl Congeners Compared to 2,3,7,8-Tetrachlorodibenzo-p-dioxin in Causing Fish Early Life Stage Mortality

Use of 2,3,7,8-tetrachlorodibenzo-p-dioxin (TCDD) toxicity equivalentsconcentration (TEC) assumes that polychlorinated di benzo-p-dioxins(PCDDs), dibenzofurans (PCDFs), and biphenyls (PCBs) act additivelyand via a common mechanism to cause toxicity. To test theseassumptions, 11 TCDD-like congeners and three non-TCDD-likecongeners were combined at ratios typically found in Lake Michiganlake trout. The potency of the mixture, expressed as TEC basedon fish-specific toxic equivalency factors, was compared toTCDD for producing lake trout and rainbow trout early life stagemortality. Signs of toxicity following exposure of newly fertilizedeggs to the mixture or to TCDD were indistinguishable; sac frymortality associated with blue-sac disease, and slopes of thedose-response curves for percentage sac fry mortality versusegg TEC or versus egg TCDD were parallel. However, the mixturedose-response curves were significantly shifted to the rightof the TCDD dose-response curves by 1.3- to 1.8-fold as illustratedby LD₅₀ values. Following exposure to the mixture or TCDD, LD₅₀sfor lake trout early life stage mortality were 97 (89–110)pg TE/g egg and 74 (70–80) pg TCDD/g (LD₅₀, 95% fiduciallimits) and for rainbow trout were 362 (312–406) pg TE/gegg and 200 (148–237) pg TCDD/g egg. These data suggestthat TCDD-like congeners act via a common mechanism to causetoxicity during trout early development, but may not act strictlyadditively when combined in a mixture of TCDD- and non-TCDD-likecongeners at ratios found in Great Lakes fish. The deviationfrom additivity, however, is less than current safety factorsof 10-fold commonly applied in ecological risk assessments,providing support for the continued use of a TE additivity modelfor assessing risk posed by complex mixtures of PCDDs, PCDFs,and PCBs to fish.     

Teratogenic potency of 2,3,4,7,8-pentachlorodibenzofuran and of three mixtures of polychlorinated dibenzo-p-dioxins and dibenzofurans in mice. Problems with risk assessment using TCDD toxic-equivalency factors

The potency of 2,3,4,7,8-pentachlorodibenzofuran (P5CDF) and of three defined 2,3,7,8-TCDD-free mixtures of polychlorinated dibenzo-p-dioxins and dibenzofurans (PCDDs/PCDFs) to induce cleft palates in NMRI mice was studied. The data were compared with a dose-response curve for 2,3,7,8-tetrachlorodibenzo-p-dioxin (TCDD). The slope of the dose-response curve for P5CDF was the same as for TCDD. However, application of the International-TCDD-Toxic-Equivalency (I-TE) factor (NATO/CCMS 1988) of 0.5 overestimated the potency of the pentachlorinated congener about 2.5-fold under these experimental conditions, suggesting 0.2 as a TE factor. When assessing the cleft palate frequency on the basis of I-TEs and the weight of the substances, the potencies of the two PCDF mixtures studied were also clearly overestimated. This result was not substantially changed when using the TE factor of 0.2 for P5CDF. For the PCDD mixture studied, the cleft palate-inducing potency found largely agreed with the prediction when applying the I-TE factors. According to our data, the use of TE factors as calculated by the UBA/BGA (1985) or the NATO/CCMS (1988) are both conservative when attempting to assess the cleft palate incidence induced by PCDF mixtures in mice.     

Highly purified hexachlorobenzene induces cytochrome P4501A in primary cultures of chicken embryo hepatocytes

Some uncertainty exists regarding the purity of hexachlorobenzene (HCB) used in past toxicity studies. It has been suggested that reported toxic and biochemical effects initially attributed to HCB exposure may have actually been elicited by contamination of HCB by polychlorinated dibenzo-p-dioxins (PCDDs) and polychlorinated dibenzofurans (PCDFs). Herein, primary cultures of chicken embryo hepatocytes (CEH) were used to compare the potencies of two lots of reagent-grade hexachlorobenzene (HCB-old [HCB-O] and HCB-new [HCB-N]), highly purified HCB (HCB-P) and 2,3,7,8-tetrachlorodibenzo-p-dioxin (TCDD) as inducers of ethoxyresorufin O-deethylase (EROD) activity, cytochrome P4501A4 (CYP1A4) messenger ribonucleic acid (mRNA) and CYP1A5 mRNA. The study also compared the EROD- and CYP1A4/5 mRNA-inducing potencies of HCB to the potencies of two mono-ortho substituted polychlorinated biphenyls (PCBs), 2,3,3′,4,4′-pentachlorobiphenyl (PCB 105) and 2,3′4,4′,5-pentachlorobiphenyl (PCB 118). HCB-O, HCB-N and HCB-P all induced EROD activity and up-regulated CYP1A4 and CYP1A5 mRNAs. Induction was not caused by contamination of HCB with PCDDs or PCDFs. Based upon a comparison of the EC₅₀ and EC_threshold values for EROD and CYP1A4/5 mRNA concentration-response curves, the potency of HCB relative to the potency of TCDD was 0.0001, and was similar to that of PCB 105 and PCB 118. The maximal EROD activity and CYP1A4/5 mRNA expression differed greatly between HCB and TCDD, and may contribute to an overestimation of the ReP value calculated for highly purified HCB.     

The Importance of Pharmacokinetics in Determining the Relative Potency of 2,3,7,8-Tetrachlorodibenzo-p-dioxin and 2,3,7,8-Tetrachlorodibenzofuran

The Importance of Pharmacokinetics in Determining the Relative Potency of 2,3,7,8-Tetrachlorodibenzo-p-dioxin and 2,3,7,8-Tetrachlorodibenzofuran. Devito, M. J., and Birnbaum, L. S. (1995). Fundam. Appl. Toxicol.24, 145-148.Polychlorinated dibenzo-p-dioxins and dibenzofurans induce exthoxyresorufin-O-deethylase (EROD) activity, a marker for CYP1A1. Differences in potency of these compounds can be attributed to differences in their affinity for the Ah receptor as well as differences in pharmacokinetics. To test the role of pharmacokinetics in the in vivo potency of these chemicals, 2,3,7,8-tetrachlorodibenzo-p-dioxin (TCDD) and 2,3,7,8-tetrachlorodibenzufuran (TCDF) were administered to female B6C3F1 mice for 4 or 13 weeks of treatment and EROD activity in liver and skin was determined. The doses were designed to be equally potent based on the published Toxic Equivalency Factor (TEF) values for these compounds. Mice received either 150 ng TCDD/kg/day or 1500 ng TCDF/kg/day, 5 days/week for either 4 or 13 weeks. At 4 weeks, hepatic EROD was induced 11- and 7-fold by TCDD and TCDF, respectively. These data indicate that the published TEFs accurately estimated the relative potency of TCDF after 4 weeks of treatment. After 13 weeks, hepatic EROD was induced 41- and 6-fold by TCDD and TCDF, respectively. The TEFs did not accurately estimate the relative inductive potency of these compounds when compared after 13 weeks of treatment. The inability of the TEFs to predict the relative potency of these compounds after 13 weeks of treatment may be due in part to the differences in the pharmacokinetic properties of each congener. The half-life of TCDF and TCDD is approximately 2 and 15 days, respectively. Steady-state levels of TCDD were not attained by 4 weeks, which is reflected in the increase in hepatic EROD between 4 and 13 weeks. In contrast, steady-state levels of TCDF were reached within 4 weeks. Thus, induction of hepatic EROD remained constant from 4 to 13 weeks. Similar results were observed for skin EROD activity. These data demonstrate that estimates of the relative potency of two chemicals is dependent upon the dosing regimen and the time of euthanization. Thus TEFs derived from short-term assays may not adequately predict the relative potencies of this class of compounds following chronic exposure.     

A review of the aquatic ecotoxicology of polychlorinated dibenzo-p-dioxins and dibenzofurans

This paper reviews published studies on polychlorinated dibenzo-p-dioxins and polychlorinated dibenzofurans that are relevant to an assessment of their aquatic ecotoxicology. The available data suggest that laterally substituted congeners containing altogether 4,5, or 6 chlorine atoms are highly toxic, particularly to the early life stages of fish, with reported effect concentrations in the ng L¹ range. These congeners are also the most readily bioaccumulated. An aquatic toxicity threshold concentration of 0.011–0.038 ng L^?1, applicable to natural ecosystems, was determined for 2,3,7,8-tetrachlorodibenzo-p-dioxin (or for mixtures of congeners expressed as 2,3,7,8-TCDD equivalents). This threshold corresponds to the no observed effect concentration/lowest-observed effect concentration determined for mortality, growth, and behavioral effects seen in rainbow trout early life stages, exposed to 2,3,7,8-TCDD in a flow-through system over a 28-day period, followed by 28 days of depuration. An investigation was also made into the potential for using mammalian-derived toxic equivalency factors (TEFs) in aquatic ecosystems. This revealed that such an approach may underestimate the aquatic toxicity of some congeners, and that the use of organism-specific TEFs may be more appropriate. © by John Wiley & Sons, Inc.     

Absorption and tissue distribution of various polychlorinated dibenzo-p-dioxins and dibenzofurans (PCDDs and PCDFs) in the rat

A defined mixture of polychlorinated dibenzo-p-dioxins and dibenzofurans (PCDDs and PCDFs) was parenterally administered to rats and absorption and tissue distribution were measured: 1) Toluene/DMSO (1+2; v/v) proved to be a convenient vehicle for the subcutaneous administration of the various PCDDs and PCDFs. Seven days after application the rate of absorption was 90% of the administered dose or even higher for almost all of the PCDDs/PCDFs in the mixture. In a few cases only (e.g. OCDD) the rate was found to be 84–89%; 2) Seven days after subcutaneous administration all 2378-substituted congeners were found in the liver, whereas only a few non-2378-substituted congeners could be measured in minor quantities. The 2378-substituted congeners also predominated in adipose tissue; however, most of the non-2378-substituted congeners were also detected; 3) The amount deposited within the liver as percentage of the administered dose differed for the various 2378-substituted PCDDs and PCDFs, ranging from <10% for OCDD or 2378-T4CDF, and between 60 and close to 100% for 12378-P5CDD or the H6CDDs. Therefore, the concentration ratio (liver/adipose tissue) was also found to be very different, ranging from <3 in the case of 2378-T4CDD or 2378-T4CDF to >40 in the case of 1234678-H7CDD, 23478-P5CDF, 123678-H6CDF, or 1234678-H7CDF; 4) Studies performed at the time period of ongoing absorption (13–14 h after injection) provided the first evidence that some of the non-2378-substituted congeners do reach substantial concentrations in hepatic tissue shortly after administration; 5) Subsequent to intraperitoneàl injection of the same PCDD/PCDF mixture the concentrations within the liver were found to be almost identical with that found after subcutaneous injection. In contrast, much higher concentrations of the congeners were found in (abdominal) adipose tissue; 6) In the liver of untreated rats of the same strain no T4CDDs/T4CDFsAbbreviations Used PCDDs, PCDFs polychlorinated dibenzo-p-dioxins, and dibenzofurans - T4CDDs, T4CDFs tetra-chlorinated dibenzo-p-dioxins, and dibenzofurans - P5CDDs, P5CDFs penta-chlorinated dibenzo-p-dioxins, and dibenzofurans - H6CDDs, H6CDFs hexa-chlorinated dibenzo-p-dioxins, and dibenzofurans - H7CDDs, H7CDFs hepta-chlorinated dibenzo-p-dioxins, and dibenzofurans - OCDD, OCDF octa-chlorinated dibenzo-p-dioxin, and dibenzofuran - DMSO dimethylsulfoxide     

Rapid bioassay for the determination of dioxins and dioxin-like PCDFs and PCBs in meat and animal feeds

Over the past several years, the numerous contamination incidents have raised concerns over the presence of halogenated aromatic hydrocarbons, such as 2,3,7,8-tetrachlorodibenzo-p-dioxin (TCDD), and related chemicals in foods and feeds. Here we applied a sensitive recombinant mouse hepatoma cell (H1L1.1c2) bioassay for the determination of dioxins and dioxin-like polychlorinated dibenzofurans (PCDFs) and biphenyls (PCBs) in meat and animal feeds. These cells responded to TCDD-like chemicals with dose-dependent induction of firefly luciferase activity, and the minimal detection limit of TCDD in the cell was 16 fg. Induction equivalency factors determined for pure TCDD-like polychlorinated dibenzo-p-dioxins (PCDDs), PCDFs, and PCBs in the bioassay were well-correlated with the World Health Organization's toxic equivalency factors. To determine the applicability of the bioassay system to detect those compounds presence in meat and feed samples, cell bioassays for 17 TCDD-like PCDDs and PCDFs congeners-spiked lipid extracted from beef or animal feed were performed. Mean recoveries of TCDD-like chlorinated PCDDs and PCDFs congeners from spiked beef or feed fat ranged from 61.2 to 122.3%. Within-laboratory coefficients of variation for analysis as index of precision were lower than 5.2%, and the calculated limits of detection and quantitation were 0.33 and 1 pg toxicity equivalency quantity (TEQ)/0.5 g fat, respectively. Correlation between bioassay- and high-resolution gas chromatography-mass spectrometry (HR-GC-MS)-determined TEQs for 10 meat samples was 0.85, with 1.2 times higher in bioassay than HR-GC-MS. The correlation between bioassay- and HR-GC-MS-determined TEQs in 10 animal feed products was 0.81, with 2.1 times higher in bioassay than HR-GC-MS. Overall, these results demonstrated that the recombinant cell bioassay can be used for the rapid detection and quantitation of PCDDs and dioxin-like PCDFs and PCBs in meats and animal feeds.     

A comparative study of polychlorinated dibenzofurans,polychlorinated biphenyls and 2,3,7,8-tetrachlorodibenzo-p-dioxin on aryl hydrocarbon hydroxylase inducing potency in rats

The aryl hydrocarbon hydroxylase (AHH) inducing potency of toxic chlorinated aromatic hydrocarbons such as polychlorinated dibenzofurans (PCDFs), polychlorinated biphenyls (PCBs) and 2,3,7,8-tetrachlorodibenzo-p-dioxin (TCDD) was studied in the young male Wistar rats. Alternatively, a technical PCDF mixture, 15 individual PCDF isomers or TCDD were administered i.p. in doses of 5 g/kg; a PCB mixture was given in a dose of 50 mg/kg. The order of AHH inducing ability was TCDD > PCDFs PCBs in kidney, lung, and liver. In the prostate, thymus, and spleen, only TCDD enhanced the AHH activity. The AHH inducibility in the lung and liver, induced by 15 pure PCDF isomers with varying chlorine substitutions was also examined. Only 2,3,7,8-tetrachlorodibenzofuran (2,3,7,8-tetra-CDF) and 2,3,4,7,8-pentachlorodibenzofurans (2,3,4,7,8-penta-CDF) significantly induced the hepatic AHH activity (4- and 2-fold, respectively), while eight PCDF isomers, including these two, significantly enhanced the pulmonary AHH activity (6- to 30-fold). Taking into account both the potent AHH inducibility and the high bioaccumulation of these compounds, 2,3,7,8-tetra- and 2,3,4,7,8-penta-CDF should be given due attention with regard to environmental-related factors and the possibility of involvement in the etiology of Yusho disease.A part of this work was presented at the 51st annual meeting of the Japanese Society for Hygiene, May 1–3, 1981, Sapporo, Japan and the 52nd annual meeting of the Japanese Society for Hygiene, March 29–31, 1982, Tokyo, Japan     

Differential relative effect potencies of some dioxin-like compounds in human peripheral blood lymphocytes and murine splenic cells

Human risk assessment for dioxin-like compounds is typically based on the concentration measured in blood serum multiplied by their assigned toxic equivalency factor (TEF). Consequently, the actual value of the TEF is very important for accurate human risk assessment. In this study we investigated the effect potencies of three polychlorinated dibenzo-p-dioxins (PCDDs), six polychlorinated dibenzofurans (PCDFs) and 10 polychlorinated biphenyls (PCBs) relative to the reference congener 2,3,7,8-tetrachloro-dibenzo-p-dioxin (TCDD) in in vitro exposed primary human peripheral blood lymphocytes (PBLs) and mouse splenic cells. REPs were determined based on cytochrome P450 (CYP) 1A1, 1B1 and aryl hydrocarbon receptor repressor (AhRR) gene expression as well as CYP1A1 activity in human PBLs and Cyp1a1 gene expression in murine splenic cells. Estimated median human REPs for 1,2,3,4,6,7,8-heptachlorodibenzo-p-dioxin (1234678-HpCDD), 2,3,4,7,8,-pentachlorodibenzofuran (23478-PeCDF), 1,2,3,4,7,8-hexachlorodibenzofuran (123478-HxCDF) and 1,2,3,4,7,8,9-heptachlorodibenzofuran (1234789-HpCDF) were with 0.1, 1.1, 1 and 0.09, respectively, significantly higher compared to those estimated for mouse with REPs of 0.05, 0.45, 0.09 and 0.04, respectively. Opposite to these results, the estimated median human REP of 3,3′,4,4′,5-pentachlorobiphenyl (PCB 126), was with 0.001 30-fold lower compared to the mouse REP of 0.03. Furthermore, human REPs for 1234678-HpCDD, 23478-PeCDF, 123478-HxCDF, 1234789-HpCDF and PCB 126 were all outside the ± half log uncertainty range that is taken into account in the WHO-assigned TEFs. Together, these data show congener- and species-specific differences in REPs for some, but not all dioxin-like congeners tested. This suggests that, more emphasis should be placed on human-tissue derived REPs in the establishment of a TEF for human risk assessment.     

Elimination of various polychlorinated dibenzo-p-dioxins and dibenzofurans (PCDDs and PCDFs) in rat faeces

A defined mixture (of a composition characteristic of that present in incinerator fly ash) of polychlorinated dibenzo-p-dioxins and -furans (PCDDs and PCDFs) was subcutaneously administered to rats and the elimination of the unchanged congeners via faeces was measured. 1) All congeners administered could be found in faeces. 2) The rates of elimination via faeces were rather different for the different congeners. 3) The most toxic congeners, 2378-T4CDD and 12378-P5CDD, were present in unmetabolized form in faeces to < 4% and < 8% of the administered dose within the first week. Thus, parenteral administration clearly minimizes contamination of the animal quarters when compared with corresponding oral dosing. 4) The rate of unchanged elimination was apparently especially pronounced for the higher chlorinated PCDDs and PCDFs. The highest excretion rate was found for 1234678-H7CDD (up to 30% of administered dose). 5) No obvious differences were observed in the rates of elimination of the unchanged substances via faeces of the 2378-substituted or the non-2378-substituted isomers.Abbreviations Used PCDDs PCDFs polychlorinated dibenzo-p-dioxins, and -furans - T4CDDs T4CDFs tetra-chlorinated dibenzo-p-dioxins, and -furans - P5CDDs P5CDFs penta-chlorinated dibenzo-p-dioxins, and -furans - H6CDDs H6CDFs hexa-chlorinated dibenzo-p-dioxins, and -furans - H7CDDs H7CDFs hepta-chlorinated dibenzo-p-dioxins, and -furans - OCDD OCDF octa-chlorinated dibenzo-p-dioxin, and-furan - DMSO dimethyl-sulfoxide     

Relative Liver Tumour Promoting Activity and Toxicity of some Polychlorinated Dibeiizo-p-dioxin- and Dibenzofuran-Congeners in Female Sprague-Dawley Rats

Abstract: The polychlorinated dibenzo-p-dioxins/dibenzofurans 1,2,3,7,8-pentachlorodibenzo-p-dioxin (PeCDD), 2,3,7,8-tetrachlorodibenzo-p-dioxin (TCDD) and 2,3,4,7,8-pentachlorodibenzofuran (PeCDF) were studied for liver tumour promoting activity in a medium-term altered foci assay in nitrosamine-initiated female Sprague-Dawley rats. The congeners under study were administered by weekly subcutaneous injections at three dose levels for 20 weeks. Evaluation of γ-glutamyl-transpeptidase (GGT⁺), altered hepatic foci development, showed that all congeners studied acted as potent promoters of hepatocarcinogenesis. TCDD and PeCDD were virtually equipotent as enhancers of foci development while PeCDF displayed approximately ten per cent of the activity of the dioxins. Analysis of the dioxin- and furan-congeners by gas chromatography/mass spectroscopy (GC/MS) technique showed that the retention of PeCDD and PeCDF in liver tissue was approximately 7 and 20 times, respectively, as high as the retention of TCDD. Based on the concentration of the respective congener in liver tissue, PeCDD and PeCDF were 0.14 and 0.007 times as active as TCDD as promoters of foci development. The dose related enhancement of GGT⁺ foci development induced by the PCDD/PCDF congeners was accompanied by an increased incidence of histological changes in the liver.     

Endocrine disrupting chemicals—Linking internal exposure to vitellogenin levels and ovotestis in Abramis brama from Dutch surface waters

The exposure of male bream from three Dutch freshwater locations to endocrine disrupting compounds (EDCs) and corresponding effects are described in this study. Fish specimen displaying reproductive disorders associated with high levels of plasma vitellogenin (VTG) concentrations and occurrence of ovotestis (OT) were investigated. To provide information on the full spectrum of EDCs in fish tissue, adipose tissue samples of individual fish were analyzed for nearly 130 chemicals targeting different compound classes (bisphenols, alkylphenols, pesticides, polychlorinated dibenzo-p-dioxins (PCDDs), dibenzofurans (PCDFs), polychlorinated biphenyls (PCBs), hydroxylated polychlorinated biphenyls (OH-PCBs), polybrominated diphenyl ethers (PBDEs) and biphenyls (PBBs)) and steroid hormones. To establish whether tissue from specimen with reproductive disorders shows a spectrum of EDCs that is qualitatively and quantitatively different from that of controls free of symptoms, bioassay-directed fractionation was performed using the recombinant yeast estrogen screen (YES), the E-Screen bioassay, the human sulfotransferase 1E1 (SULT1E1) inhibition assay, and the coumestrol-based estrogen receptor α (ERα) high resolution screening (HRS) assay. No differences in estrogenicity could be observed between the cases and controls and steroidal estrogens accounted for the majority of estrogenicity found in the complex mixtures. In this study, the combination of the different assays employed to measure total estrogenicity and the SULT1E1 inhibition does not predict the outcome of unwanted physiological effects, however, it can be used to determine the presence of EDCs in fish samples and their estrogenic effects.     

Ethoxyresorufin-O-deethylase (EROD) induction by TCDD,PeCDF and PCB 126 in bobwhite quail hepatocytes

World Health Organization (WHO) toxic equivalency factors are used to calculate toxic equivalent (TEQ) concentrations of complex mixtures of dioxin-like compounds (DLCs), such as polychlorinated dibenzo-p-dioxins, polychlorinated dibenzofurans and polychlorinated biphenyls (PCBs), for mammals, fish and birds. The TEQ concept assumes that all species of a taxa respond with similar sensitivity to individual DLCs, but several reports do not support this assumption for birds. Our laboratory is conducting research to attempt to uncover the fundamental mechanism(s) underlying the reasons why avian species differ in sensitivity to DLCs. The present study determined concentration-dependent effects of 2,3,7,8-tetrachlorodibenzo-p-dioxin (TCDD), 2,3,4,7,8-pentachlorodibenzofuran (PeCDF) and 3,3′,4,4′,5-pentachlorobiphenyl (PCB 126) on ethoxyresorufin-O-deethylase (EROD) activity in primary cultures of northern bobwhite quail (Colinus virginianus) hepatocytes. Bobwhite quail were studied because (1) this species is used in the laboratory for toxicity testing and (2) the amino acids at all locations within the ligand binding domain (LBD) of aryl hydrocarbon receptor 1 (AHR1) in bobwhite quail and ring necked pheasant (Phasianus colchicus) are identical. Because earlier work indicated the importance of the identity of amino acids at key sites within the AHR1 LBD, we hypothesized that bobwhite quail and ring necked pheasant hepatocytes should have similar sensitivity to EROD induction by DLCs. EC_threshold-based relative sensitivity of the bobwhite quail compared to chicken for TCDD, PeCDF and PCB 126 was 0.11, 0.17 and 0.02, respectively. The rank order of potency was PeCDF > TCDD > PCB 126. The results confirm that bobwhite quail and ring-necked pheasant hepatocytes have similar sensitivity to EROD induction by TCDD, PeCDF and PCB 126.     

Persistence of various polychlorinated dibenzo-p-dioxins and dibenzofurans (PCDDs and PCDFs) in hepatic and adipose tissue of marmoset monkeys

A defined mixture of polychlorinated dibenzo-p-dioxins and dibenzofurans (PCDDs and PCDFs) was subcutaneously administered to marmoset monkeys (Callithrix jacchus). Tissue concentrations in hepatic and adipose tissue were measured at different times after treatment (1–28 weeks). One week after application high concentrations could be detected for the 2,3,7,8-substituted congeners only. The percent of the administered dose in whole liver differed for the various 2,3,7,8-substituted congeners, ranging from 24.5±4.5% for 2,3,7,8-TCDD to 74.1±4.9% for 2,3,4,6,7,8-H6CDF. Therefore, the concentration ratio (liver/adipose tissue) was also very different, ranging from about 1 (2,3,7,8-T4CDD or 2,3,7,8-T4CDF) to >10 in the case of some higher chlorinated PCDDs and PCDFs. Half-lives of PCDDs and PCDFs were very different for the various 2,3,7,8-substituted congeners. For the most toxic compound (2,3,7,8-T4CDD) a t/2 of about 8 weeks in hepatic tissue and about 11 weeks in adipose tissue was found when calculated from data obtained later than 6 weeks after injection. For 2,3,7,8-T4CDD and 1,2,3,7,8-P5CDD the decreases in hepatic concentrations were much faster during the first 6 weeks after administration (t/2 of 4 weeks). This was apparently due to redistribution phenomena. Half-life increased with increasing degrees of chlorination. In some cases (e.g. OCDD, OCDF) no significant decrease in tissue concentrations could be observed after 28 weeks. The shortest t/2 was determined for 2,3,7,8-T4CDF: shorter than 6 days in hepatic tissue and about 10 days in adipose tissue. Calculation of the body burden of thenon-2,3,7,8-substituted PCDDs/PCDFs 1 week after injection revealed that all groups of isomers were present at less than 5%. Consequences of these findings for the use of TCDD-toxic-equivalency factors are discussed and a change in strategy is suggested.Data presented in this paper are part of the doctoral thesis of Thomas Wiesmüller submitted to the Fakultät für Chemie und Pharmazie, Eberhard-Karls-Universität, Tübingen     

Reproductive success of three passerine species exposed to dioxin-like compounds near Midland,Michigan, USA

Nests of three passerine birds, house wren (HOWR), tree swallow (TRES), and eastern bluebird (EABL) were monitored daily (2005–2007) at study areas (SAs) downstream of Midland, Michigan where soil and sediment concentrations of polychlorinated dibenzofurans (PCDFs) were significantly greater than the regional background concentrations and upstream reference areas (RAs). Similarly, TRES research conducted at sites contaminated with dioxin-like compounds indicated that concentrations of polychlorinated dibenzo-p-dioxins and PCDFs, expressed as ΣPCDD/DFs and 2,3,7,8-tetrachlorodibenzo-p-dioxin equivalents observed in the diet and eggs of these three species would be predicted to cause significant effects on reproduction. However, site-specific reproductive parameters including hatching success and fledging success at downstream SAs were similar to or greater than those at upstream RAs. Specifically, hatching success was not significantly different among years, species, locations, or between early and late nesting attempts. Of all initiated clutches, 66% (n = 427), 73% (n = 245), and 64% (n = 122) successfully fledged at least one nestling for HOWR, TRES, and EABL, respectively. Overall reproductive performance was similar between SAs and RAs. The reason for these unexpected results is consistent with the fact that there are species-specific and congener-specific differences in sensitivities to the effects of aryl hydrocarbon receptor agonists.     

Liver-specific decrease in Tff3 gene expression in infant mice perinatally exposed to 2,3,7,8-tetrabromodibenzofuran or 2,3,7,8-tetrachlorodibenzo-p-dioxin

Polybrominated dibenzo-p-dioxins and dibenzofurans (PBDD/DFs) are byproducts of brominated flame retardants and can cause adverse health effects. Although exposure to polychlorinated (PC) DD/DFs induces toxic effects, including liver injury and neurobehavioral disorder, little is known about toxicities associated with PBDD/DF exposure. Thus, we examined effects of perinatal exposure to brominated congener on the infant mouse. Gene expression in several organs, such as the liver and brain, was analyzed in mouse offspring born to dams administered 2,3,7,8-tetrabromodibenzofuran (TBDF; 9 or 45 μg/kg body weight) or 2,3,7,8-tetrachlorodibenzo-p-dioxin (TCDD; 3 μg/kg body weight) on gestational day 12.5. An increase in liver size was observed in TBDF- or TCDD-exposed offspring in infancy. Gene microarray analysis revealed that 163 and 36 genes were markedly upregulated and downregulated, respectively, in the liver of TBDF-exposed mice compared with those in vehicle-treated mice on postnatal day (PND) 5. Significant increases in Cyp1a1, Cyp1a2, Fmo3, and Pnliprp1 and decreases in Tff3, Ocstamp, Kcnk16, and Lgals2 mRNA levels in TBDF-exposed offspring on PNDs 5 and 12 were confirmed by quantitative PCR. In particular, a significant reduction in Tff3 mRNA in the liver, but not in the brain, small intestine, colon, and kidney, was observed in offspring perinatally exposed to TBDF or TCDD. Ultrasonic calls of TBDF- or TCDD-exposed offspring on PNDs 3–5 were impaired. Taken together, perinatal exposure to polyhalogenated dioxin/furan congeners disrupts gene expression patterns in the liver and ultrasonic calling during infancy. These results suggest that liver injury may contribute to neurobehavioral disorder.     

Teratogenic effects of 2,3,7,8-tetrabromodibenzo-p-dioxin and three polybrominated dibenzofurans in C57BL/6N mice

Brominated flame retardants involved in many industrial uses contain polybrominated dibenzo-p-dioxins (PBDDs) and dibenzofurans (PBDFs) as contaminants. The levels of these contaminants can be dramatically increased by combustion. These chemicals are closely related in structure to the polychlorinated dibenzo-p-dioxins (PCDDs) and dibenzofurans (PCDFs), of which 2,3,7,8-tetrachloridibenzo-p-dioxin (TCDD) is the most toxic isomer. TCDD and related PCDFs are potent mouse teratogens inducing cleft palate and hydronephrosis at doses below those at which overt maternal and embryo/fetal toxicity occurs. This study examines the teratogenic effects of 2,3,7,8-tetrabromodibenzo-p-dioxin (TBDD), 2,3,7,8-tetrabromodibenzofuran (TBDF), 1,2,3,7,8-pentabromodibenzofuran (1PeBDF), and 2,3,4,7,8-pentabromodibenzofuran (4PeBDF) in C57BL/6N mice treated on gestation day (gd) 10 and examined on gd 18. Pregnant dams were treated with 0-4000 micrograms of each congener per kilogram body weight in 10 ml corn oil/kg. Dose selection was based on the relative toxicity of the chlorinated isomers. Maternal toxicity and developmental toxicity were assessed, and the hard palate and kidney, the target organs for the teratogenic effects of TCDD and related compounds, were examined for structural abnormalities. While the maternal liver weight increased at all dose levels examined for all four compounds, there was no evidence of any maternal toxicity. Embryo/fetal mortality was increased only at greater than or equal to 500 microgram TBDF/kg, while fetal weight increased in a dose-related manner following exposure to TBDD and TBDF. All compounds produced hydronephrosis (HN) at doses below that at which cleft palate (CP) occurred. The incidence of HN was significantly increased above background levels at the following doses (micrograms/kg): TBDD, 3; TBDF, 25; 1PeBDF, 500; 4PeBDF, 400. The LOELs (micrograms/kg) for CP were: TBDD, 48; TBDF, 200; 1PeBDF, 4000; 4PeBDF, 2400. The cleft palate incidence for all four brominated compounds and TCDD could be fit to a common slope, compatible with the concept that these chemicals all exert their teratogenic effects through a common mechanism. The potency of these chemicals, relative to TCDD as 1 for the induction of cleft palate, is TBDD, 0.24; TBDF, 0.10; 1PeBDF, 0.004; and 4PeBDF, 0.005. Previous studies from our laboratory had determined that the chlorinated dibenzofuran isomers had relative potencies of 0.05 (TCDF), 0.03 (1PeCDF), and 0.09 (4PeCDF). Thus, bromination decreases the teratogenic activity of TBDD relative to TCDD and of both 1- and 4PeBDF relative to the chlorinated isomers. However, substitution of bromines for chlorines increases the potency of TBDF relative to TCDF.(ABSTRACT TRUNCATED AT 400 WORDS)     

Transfer of Polychiorinated Dibenzo-p-dioxins and Dibenzofurans to Fetal and Neonatal Rats

A fly ash extract from a municipal incinerator, containing polychlorinateddibenzo-p-dioxins (PCDDs) and dibenzofurans (PCDFs), was orallyadministered to rats on Days 10 to 17 of the pregnancy and duringthe first 10 days of the lactation period. PCDD and PCDF congenersretained in the fetuses and livers of the offspring had a 2,3,7,8-chlorinesubstitution pattern. The only non-2,3,7,8-substituted congenerretained in the liver of the offspring and females was 2,3,4,6,7-pentachlorodibenzofuran(PnCDF). In the fetuses 2,3,7,8-tetrachlorodibenzo-p-dioxin(TCDD) had the highest retention (0.13% of total dose) and adecrease in retention was found with increasing number of chlorineatoms. In the livers of the offspring, the highest retentionwas found for 2,3,7,8-TCDD and the three 2,3,7,8-substitutedhexachlorodibenzo-p-dioxins (HxCDDs) (5.26–8.12%). Inthe livers of the pregnant and lactating females penta- andhexachlorinated congeners had the highest retention (53.91–80.20%). For both groups the liver retention of the tetra- tooctachlorinated congeners was similar, but the lactating femalesstored less PCDDs and PCDFs in their adipose tissue. A linearrelationship was found between the retention of congeners inthe livers of the females and offspring.