Interactive Effects of Three Structurally Different Polychlorinated Biphenyls in a Rat Liver Tumor Promotion Bioassay

Interactive effects between the non-ortho-substituted 3,3′, 4,4′,5-pentachlorobiphenyl (PCB126), the mono-ortho-substituted 2,3,3′,4,4′-pentachlorobiphenyl (PCB105), and the di-ortho-substituted 2,2′,4,4′,5,5′-hexachlorobiphenyl (PCB153) were studied in an initiation/promotion bioassay. Female Sprague–Dawley rats were injected with 30 mg/kg ip ofN-nitrosodiethylamine 24 h after partial hepatectomy. Five weeks later, weekly sc administrations of the three PCBs in 15 systematically selected dose combinations started. After 20 weeks of administration, the animals were killed and the livers were analyzed for areas expressing placental glutathione-S-transferase as a marker of preneoplastic foci. In addition, concentration of liver and kidney retinoids and plasma retinol was analyzed, as well as body and organ weights, plasma transaminases, and induction of hepatic cytochrome P450 1A1/2 (CYP1A1/2) and CYP2B1/2 activities. Data were analyzed with a multivariate method. At the doses applied in this study, weak antagonism was observed between PCB126 and PCB153 for effects on volume fraction of foci, number of foci/cm³, concentration of plasma retinol and liver retinoids, relative liver weight, and induction of CYP2B1/2 activity. Weak antagonism was also observed between PCB126 and PCB105 for effects on volume fraction of foci, number of foci/cm³, and plasma retinol concentration. No interactions other than pure additivity were observed between PCB105 and PCB153. Synergism was not observed within the dose ranges investigated in this study. Knowledge of interactive effects is important for risk assessment of environmental mixtures of dioxin-like compounds. Antagonism between congeners generally results in risk assessments that overestimate human risk. The significance to human risk assessment of the relatively weak antagonism observed in this study is however unclear, considering many other uncertainties involved in the toxic equivalency factor (TEF) concept. A change of the TEF concept for risk assessments of dioxin-like substances is not motivated based on the results of this study.     

Effects of subchronic exposure to complex mixtures of dioxin-like and non-dioxin-like polyhalogenated aromatic compounds on thyroid hormone and vitamin A levels in female Sprague-Dawley rats.

The aim of this study was to determine the effects of subchronic exposure to complex mixtures of polyhalogenated aromatic hydrocarbons (PHAHs) on the thyroid hormone and retinoid status in female Sprague-Dawley rats and to investigate the predictability of these effects by the toxic equivalency factor (TEF) concept. In the first experiment, the focus was on a complex dioxin-like PHAH mixture, which covered > 90% of the total toxic equivalents (TEQ) present in Baltic herring. In the second experiment, the contribution of non-dioxin-like polychlorinated biphenyls (PCBs) was investigated by testing the commercial PCB mixture Aroclor 1260, its 0-1 ortho and 2-4 ortho fractions and the reconstituted 0-4 ortho fraction. Hepatic retinoid levels were severely decreased ( approximately 70%) after treatment with the dioxin-like PHAH mixture, similar to the effect of a TEQ equivalent dose of 1 microg 2,3,7,8-TCDD/kg bw/week. However, the TEF concept failed to predict the effect on plasma retinol; a decrease (21%) was observed after treatment with the PHAH mixture, whereas an increase (21%) was found after treatment with TCDD. A more severe decrease of total thyroid hormone in plasma was observed after exposure to the PHAH mixture compared to treatment with TCDD ( approximately 60% vs. 38%). The discrepancy found between the predicted and observed effects for plasma retinol and thyroid hormone is possibly due to an additional effect of hydroxylated PCBs, formed from metabolizable PCBs present in the PHAH mixture. Aroclor 1260 and its fractions did not significantly alter the retinoid and thyroid hormone status at the dose levels tested, indicating that in case of exposure to complex PCB mixtures at environmental levels, no effects, or at best, only marginal effects can be expected on the retinoid and thyroid hormone status.     

CYP1A1-inducing potency in H4IIE cells and chemical composition of technical mixtures of polychlorinated biphenyls

Polychlorinated biphenyls (PCBs) are present in environmental and tissue samples as complex mixtures of dioxin-like and non-dioxin-like congeners. Induction of cytochrome (CYP) P4501A1-catalyzed 7-ethoxyresorufin-O-deethylase (EROD) activity in H4IIE hepatoma cells is widely used as a simple in vitro bioassay for the dioxin receptor-mediated biological action of dioxin-like agonists. Since the results of the assay may be influenced indirectly by abundant non-dioxin-like PCBs, its application to the bioanalysis of complex PCB mixtures was studied. In the PCB mixtures Arochlor 1254 and Clophen A50, potent dioxin-like non-ortho PCBs and polychlorinated dibenzofurans (PCDFs) were found in minor amounts. However, the non-ortho PCBs accounted for most of the overall 2,3,7,8-tetrachlorodibenzo-p-dioxin (TCDD) equivalents based on EROD induction (EROD-TEQs). A comparison with a pattern of toxic equivalents (TEQs) based on toxic equivalency factors (I-TEFs) recently suggested in an international report revealed a much higher relative impact of mono-ortho PCBs on I-TEQs than on EROD-TEQs while total EROD-TEQs approximately coincided with total I-TEQs. It is concluded that the H4IIE bioassay is useful to assess total I-TEQs but does not reflect the individual contributions of PCB subgroups because of a higher evaluation of mono-ortho and di-ortho PCBs by I-TEFs. Based on individual EROD-TEFs, slightly higher mean EROD-TEQs than those calculated by assuming additive behaviour of single PCBs were obtained. This finding suggests a minor synergistic influence of non-dioxin-like PCBs on the inducing potency of dioxin-like agonists in the H4IIE bioassay.     

The 2005 World Health Organization reevaluation of human and Mammalian toxic equivalency factors for dioxins and dioxin-like compounds.

In June 2005, a World Health Organization (WHO)-International Programme on Chemical Safety expert meeting was held in Geneva during which the toxic equivalency factors (TEFs) for dioxin-like compounds, including some polychlorinated biphenyls (PCBs), were reevaluated. For this reevaluation process, the refined TEF database recently published by Haws et al. (2006, Toxicol. Sci. 89, 4-30) was used as a starting point. Decisions about a TEF value were made based on a combination of unweighted relative effect potency (REP) distributions from this database, expert judgment, and point estimates. Previous TEFs were assigned in increments of 0.01, 0.05, 0.1, etc., but for this reevaluation, it was decided to use half order of magnitude increments on a logarithmic scale of 0.03, 0.1, 0.3, etc. Changes were decided by the expert panel for 2,3,4,7,8-pentachlorodibenzofuran (PeCDF) (TEF = 0.3), 1,2,3,7,8-pentachlorodibenzofuran (PeCDF) (TEF = 0.03), octachlorodibenzo-p-dioxin and octachlorodibenzofuran (TEFs = 0.0003), 3,4,4',5-tetrachlorbiphenyl (PCB 81) (TEF = 0.0003), 3,3',4,4',5,5'-hexachlorobiphenyl (PCB 169) (TEF = 0.03), and a single TEF value (0.00003) for all relevant mono-ortho-substituted PCBs. Additivity, an important prerequisite of the TEF concept was again confirmed by results from recent in vivo mixture studies. Some experimental evidence shows that non-dioxin-like aryl hydrocarbon receptor agonists/antagonists are able to impact the overall toxic potency of 2,3,7,8-tetrachlorodibenzo-p-dioxin (TCDD) and related compounds, and this needs to be investigated further. Certain individual and groups of compounds were identified for possible future inclusion in the TEF concept, including 3,4,4'-TCB (PCB 37), polybrominated dibenzo-p-dioxins and dibenzofurans, mixed polyhalogenated dibenzo-p-dioxins and dibenzofurans, polyhalogenated naphthalenes, and polybrominated biphenyls. Concern was expressed about direct application of the TEF/total toxic equivalency (TEQ) approach to abiotic matrices, such as soil, sediment, etc., for direct application in human risk assessment. This is problematic as the present TEF scheme and TEQ methodology are primarily intended for estimating exposure and risks via oral ingestion (e.g., by dietary intake). A number of future approaches to determine alternative or additional TEFs were also identified. These included the use of a probabilistic methodology to determine TEFs that better describe the associated levels of uncertainty and "systemic" TEFs for blood and adipose tissue and TEQ for body burden.     

Development of TEFs for PCB congeners by using an alternative biomarker — Thyroid hormone levels

Polychlorinated biphenyls (PCBs) are ubiquitous toxic contaminants. Health risk assessment for this class of chemicals is complex: the current toxic equivalency factor (TEF) method covers dioxin-like (DL-) PCBs, dibenzofurans, and dioxins, but excludes non-DL-PCBs. To address this deficiency, we evaluated published data for several PCB congeners to determine common biomarkers of effect. We found that the most sensitive biomarkers for DL-non-ortho-PCB 77 and PCB 126 are liver enzyme (e.g., ethoxyresorufin-O-deethylase, EROD) induction, circulating thyroxine (T4) decrease, and brain dopamine (DA) elevation. For DL-ortho-PCB 118 and non-DL-ortho-PCB 28 and PCB 153, the most sensitive biomarkers are brain DA decrease and circulating T4 decrease. The only consistent biomarker for both DL- and non-DL-PCBs is circulating T4 decrease. The calculated TEF-_TH, based on the effective dose to decrease T4 by 30% (ED₃₀) with reference to 2,3,7,8-tetrachlorodibenzo-p-dioxin (TCDD), is identical to both TEF-_WHO98 and TEF-_WHO05 for TCDD and DL-PCBs (correlation coefficients are r = 1.00, P < 0.001; and r = 0.99, P < 0.001, respectively). We conclude that T4 decrease is a prospective biomarker for generating a new TEF scheme which includes some non-DL-congeners. The new TEF-_TH parallels the TEF-_WHO for DL-PCBs and, most importantly, is useful for non-DL-PCBs in risk assessment to address thyroid endocrine disruption and potentially the neurotoxic effects of PCBs.     

Genotoxic effects of polychlorinated biphenyls (PCB 153, 138, 101, 118) in a fish cell line (RTG-2)

Polychlorinated biphenyls (PCBs) are persistent pollutants in aquatic environments, often causing the decline or disappearance of wild populations. The primary aim of this study was to investigate the genotoxic effects of some PCBs (PCB153 (2,2′,4,4′,5,5′-hexachlorobiphenyl) and 138 (2,2′,3,4,4′,5′-hexachloro-biphenyl), both non-dioxin-like compounds, and the pentachlorobiphenyls PCB118 (2,3′,4,4′,5-) and 101 (2,2′,4′,5,5′-), the former an ortho-substituted, low-affinity dioxin-like compound and the latter a non-coplanar congener classified as non-dioxin-like) in fish cells (RTG-2). These congeners are mostly present in surface waters and in edible aquatic organisms and the loss of DNA integrity in vitro serves as a sensitive biomarker of cytogenetic alterations and is considered as an initial step for the identification of genotoxic effects.The alkaline comet assay and the micronucleus test show clear genotoxic damage after short and longer exposure (2 and 24 h) to maximum soluble, non-cytotoxic doses, evident sooner with PCBs 101 and 118. Oxidative stress situations involving ROS release, reduction in total GSH, lipid peroxidation and alteration to superoxide dismutase, seen after exposure with all the congeners, though with different kinetics, seem the most likely explanation for the genotoxic damage. This appears to be confirmed by the modified comet assay (pH 10) for detection of oxidized bases using endonuclease III. The increased generation of intracellular ROS might explain the apoptosis seen after treatment with the single PCBs and evaluated on the basis of the rise in 3-7 caspase activity. Therefore both the non-coplanar, non-dioxin-like PCBs (153, 138, 101) and the low-affinity dioxin-like compound PCB118 cause evident genotoxic damage, probably as a consequence of oxidative stress.     

PCB concentrations in some foods from four European countries.

Samples of salmon, butter and cabbage from Belgium, Italy, Spain and Portugal were analysed for their content in total, non-dioxin-like (as represented by the so-called seven indicator-PCBs: congeners 28, 52, 101, 118, 138, 153 and 180) and dioxin-like PCBs (mono-ortho and non-ortho PCBs). Salmon and cabbage from Belgium, and butter from Portugal and Belgium, contained less total and non-dioxin-like PCBs than those from other countries. Samples from Italy had the highest concentrations. Similar patterns were observed for dioxin-like PCBs (as represented by the TCDD-equivalents of toxicity, WHO-TEQs), with the lowest values in Belgium and Portugal for salmon, in Portugal for butter and in Belgium for cabbage. Differences up to five-fold in PCB concentrations and TEQ values were seen among commodities from the four countries. The implication is that it might be worthwhile monitoring, with selection of the least contaminated commodities, to reduce the PCB exposure of the general population. This could have health consequences, because daily intakes are higher than the tolerable levels for a considerable part of the European population.     

Organochlorine pesticides and PCBs (including dl-PCBs) in human milk samples collected from multiparae from Croatia and comparison with primiparae

This study investigated the levels of 20 congeners of polychlorinated biphenyls (PCBs), including toxic dioxin-like PCBs and 7 organochlorine pesticides (OCPs) in 33 human milk samples collected in 2011 from multiparae living in Zadar, Croatia. Concentrations of ∑PCBs, ∑DDTs, ∑HCHs and HCB in samples ranged from 11.7 to 146.3, 8.7 to 89.2, 0.9 to 28.4, and <LOD to 8.0 ng g⁻¹ milk fat, respectively. PCB congeners −153, −138, −180 and −170 dominated in the PCB profiles, while p,ṕ-DDE was the most abundant OCP. PCB-126 was the most abundant non-ortho PCB, while among mono-ortho PCBs, the congeners −118, −105 and −156 equally contributed to the mono-ortho PCB fraction. TEQs for dl-PCBs ranged between 0 and 13.3 pg g⁻¹ milk fat. The calculated estimated daily intakes for all compound groups were below the tolerable daily intake indicating no risk for breastfed infants. A comparison of our results with our previous study on primiparae revealed that the concentrations of the main contaminant groups are lower in the milk of multiparae, with the exception of toxic mono-ortho PCBs whose concentrations and TEQ remained similar among the groups, and HCB whose concentrations were found to be higher in multiparae. Concentrations of PCBs and OCPs found in the samples from this study did not exceed those from other parts of the world. This study revealed that there are differences in contaminant concentrations depending on the mothers’ parity and that this fact should be taken into account when risk assessment studies are conducted.     

Effects of PCB 52 and PCB 77 on cell viability, [Ca(2+)](i) levels and membrane fluidity in mouse thymocytes

Exposure to polychlorinated biphenyls (PCBs) is known to suppress immune system function and this action is usually ascribed to dioxin-like PCBs that act via the Ah receptor. We have studied the effects of one ortho-substituted, non-dioxin-like PCB (PCB 52) and one coplanar, dioxin-like congener (PCB 77) on properties of thymocytes acutely isolated from mice. Viability of thymocytes was dose- and time-dependently reduced by PCB 52 with a threshold concentration of about 1 microM, while there was no effect of PCB 77 on viability at concentrations less than 10 microM. Cell death was detectible within 5 min of exposure. Both congeners caused a dose-dependent increase in [Ca(2+)](i), but the threshold concentration was 1 microM for PCB 52 and 5 microM for PCB 77. However, the cell death was not due to the elevation of [Ca(2+)](i), since it was not reduced by incubation in Ca-free Tyrode's Solution. PCB 52, but not PCB 77, caused an increase in membrane fluidity at a concentration of 5 microM. These observations are consistent with previous results that suggest that ortho-substituted PCB congeners dissolve in cell membrane and cause greater disruption of function than do dioxin-like PCB congeners.     

Resistance to Cyp3a induction by polychlorinated biphenyls,including non-dioxin-like PCB153, in gills of killifish (Fundulus heteroclitus) from New Bedford Harbor

Previous reports suggested that non-dioxin-like (NDL) PCB153 effects on cytochrome P450 3A (Cyp3a) expression in Atlantic killifish (Fundulus heteroclitus) gills differed between F0 generation fish from a PCB site (New Bedford Harbor; NBH) and a reference site (Scorton Creek; SC). Here, we examined effects of PCB153, dioxin-like (DL) PCB126, or a mixture of both, on Cyp3a56 mRNA in killifish generations removed from the wild, without environmental PCB exposures. PCB126 effects in liver and gills differed between populations, as expected. Gill Cyp3a56 was not affected by either congener in NBH F2 generation fish, but was induced by PCB153 in SC F1 fish, with females showing a greater response. PCB153 did not affect Cyp3a56 in liver of either population. Results suggest a heritable resistance to NDL-PCBs in killifish from NBH, in addition to that reported for DL PCBs. Induction of Cyp3a56 in gills may be a biomarker of exposure to NDL PCBs in fish populations that are not resistant to PCBs.     

Contribution of planar (0-1 ortho) and nonplanar (2-4 ortho) fractions of Aroclor 1260 to the induction of altered hepatic foci in female Sprague-Dawley rats

The hepatic tumor promoting activity of the planar 0-1 ortho ( approximately 9.7% w/w) and the nonplanar 2-4 ortho ( approximately 90.3% w/w) fraction of the commercial PCB mixture Aroclor 1260 was studied using a medium-term two-stage initiation/promotion bioassay in female Sprague-Dawley rats. Fractionation was carried out on an activated charcoal column. The composition of the effluent from the column was tested by GC-ECD. The absence of planar compounds in the 2-4 ortho fraction was confirmed by GC-MS analysis. The dioxin-like toxic potency of the fractions was determined with the DR-CALUX assay. The animal experiment was started with the initiation procedure (diethylnitrosamine injection, 30 mg/kg body wt ip, 24 h after (2)/(3) hepatectomy), followed 6 weeks later by the promotion treatment, which consisted of a weekly subcutaneous injection during 20 weeks. Exposure groups (n = 10) received the following treatments (dose/kg body wt/week): Aroclor 1260 (10 mg), 0-1 ortho fraction (0.97 mg), 2-4 ortho fraction (1, 3, or 9 mg), a reconstituted 0-4 ortho fraction (9.97 mg), 2,2',4,4',5,5'-hexachlorobiphenyl (PCB 153; 1 or 9 mg), 2,3,7,8-TCDD (1 microg; positive control) or corn oil (1 ml; vehicle control). One group did not receive a promotion treatment. All exposure groups exhibited a significantly increased volume fraction of the liver occupied by hepatic foci positive for the placental form of glutathione-S-transferase-p compared to the corn oil control, except for the groups treated with 0-1 ortho fraction and 1 mg PCB 153/kg body wt/week. Approximately 80% of the total tumor promoting capacity of the reconstituted 0-4 ortho fraction could be explained by the 2-4 ortho PCB fraction while the 0-1 ortho fraction had only a negligible contribution. These results suggest that the majority of the tumor promotion potential of PCB mixtures resides in the non-dioxin-like fraction, which is not taken into account in the toxic equivalency factor (TEF) approach for risk assessment of PCBs. This may result in an underestimation of the tumor promotion potential of environmental PCB mixtures.     

Polychlorinated biphenyls and organochlorine pesticides in human milk samples from two regions in Croatia

We analyzed 20 polychlorinated biphenyls (PCBs) and seven organochlorine pesticides (OCPs) in milk samples collected during 2009–2011 from primiparae living in two different regions in Croatia. p,p′-DDE is the dominant organochlorine pesticide. α-HCH/γ-HCH and p,p′-DDE/p,p′-DDT ratios indicate that there is fresh input of γ-HCH in investigated population on both locations, while this is not applicable to p,p′-DDT. The PCB profile was dominated by higher chlorinated congeners. Non-ortho PCB congeners which have the highest TEF values were not detected in any of individual samples. Toxic equivalents for mono-ortho substituted PCB congeners indicated higher exposure to toxic PCBs in Zadar, but estimated daily intakes for both locations indicate that infants consuming mother's milk are not at risk of adverse effects caused by PCBs and OCPs. Our study builds on the previous research of human milk samples collected in Zagreb and reveals that over 10-year period, levels of investigated organochlorine compounds decreased significantly.     

Development of a neurotoxic equivalence scheme of relative potency for assessing the risk of PCB mixtures

PCBs produce adverse effects in humans and animals by several modes of action. The first mode of action is binding of coplanar or mono-ortho-PCBs to the aryl hydrocarbon (Ah) receptor leading to effects associated with the activation of this receptor. The remaining PCB congeners do not activate this receptor and have different modes of action underlying their toxic effects. One mode of action that has been shown for di-ortho-substituted non-coplanar PCBs (PCB congeners with two or more chlorines in the ortho-positions) is the interference with intracellular signaling pathways dependent on Ca(2+) homeostasis and the resulting cellular, organ-level and organismal effects. The ortho-substituted non-coplanar congeners produce other cellular or organ-level effects including changes in protein kinase C translocation, changes in cellular dopamine (DA) uptake, formation of reactive oxygen species, and thyroid effects. Here, we propose a scheme for developing relative potency estimates (REP) for the PCB congeners not considered in the TEF scheme used to assess the toxicity of coplanar and mono-ortho-PCBs and chlorinated dioxins and furans. Because a number of the modes of action listed here for the ortho-substituted non-coplanar PCB congeners have been implicated in the neurotoxic effects of these PCBs congeners, this relative potency scheme is referred to here as the Neurotoxic Equivalent (NEQ) scheme for estimating toxicity of PCB mixtures. The Neurotoxic Equivalent (NEQ) values are developed in a way similar in concept to the derivation of the well-known TEF congener values. Although this scheme is in its infancy and the set of NEQ values are limited by the current data, there are several compelling reasons for proposing such a scheme now. First, it should open discussions as to how different modes of action can be utilized to predict congener potency differences for the effects they produce. Second, consideration and evaluation of the ability of the proposed NEQ scheme to predict the toxicity of PCB mixtures will assist in the identification of the specific modes of action relevant to the effects produced by non-coplanar PCBs. If other modes of action are suggested and subsequently identified, then other schemes of relative potency could be developed specifically for those modes of action, distinct from either the TEF scheme or the NEQ scheme. Knowing these other modes of action and the relative toxicity of the various congeners would advance our understanding of PCB toxicology and thereby ultimately improve our ability to estimate the toxic potency of PCB mixtures for each identified mode of action. Third, a quantitative scheme for assessing the toxicity of the non-coplanar PCB congeners present in a mixture has the potential to improve significantly future risk assessments of PCB mixtures.     

Reassessment of the carcinogenicity of polychlorinated biphenyls (PCBs).

The current policy for regulating polychlorinated biphenyls (PCBs) is based on one chronic bioassay that examined the carcinogenicity of a 60% chlorinated PCB (Norback & Weltman, 1985). All studies originally considered by the U.S. Environmental Protection Agency (EPA) for use in calculating a cancer slope factor (CSF) for PCBs were reevaluated and new CSFs calculated based on the results of a pathology reassessment (Moore et al., 1994). When studies of 60% chlorine PCBs from 3 different laboratories were compared, there was no scientific basis for selecting only 1 data set for deriving CSF estimates. Using a geometric mean to calculate a CSF based on all studies of PCBs with 60% chlorine replaces the current value of 7.7 (mg/kg/d)(-1) with a value of 1.9 (mg/kg/d)(-1). CSFs for PCBs containing less than 60% chlorine (54% and 42%) were less than 1.0 (mg/kg/d)(-1). Using a toxic equivalency factor (TEF) approach similar to that of 2,3,7,8-tetrachlorodibenzo-p-dioxin shows no correlation between toxic equivalent dose and CSFs, indicating that use of TEFs is not predictive of cancer potency for PCBs. Based on these findings, PCB cancer risk assessment policy would more closely reflect scientific data if (1) separate risk assessments were developed for each major PCB formulation and (2) all appropriate data were used when calculating cancer potency for PCB mixtures of 60% chlorine.     

Dioxins, dioxin-like PCBs and non-dioxin-like PCBs in foodstuffs: occurrence and dietary intake in The Netherlands

Data on occurrence of dioxins (polychlorinated dibenzo-p-dioxins [PCDDs] and dibenzofurans [PCDFs]), dioxin-like PCBs (polychlorinated non-ortho and mono-ortho biphenyls) and non-dioxin-like PCBs (as represented by the so-called indicator-PCBs: congeners 28, 52, 101, 118, 138, 153 and 180) in food products consumed in The Netherlands that were collected in measurement programs carried out during 1998 and 1999, and combined with food consumption data to assess the dietary intake of these persistent food contaminants. The estimated median life-long-averaged intake of the sum of dioxins and dioxin-like PCBs in the population is 1.2 pg WHO-TEQ (toxic equivalents) per kg body weight (bw) per day, while the estimated median life-long-averaged intake of indicator-PCBs is 5.6 ng per kg bw per day. The contribution of different food groups to the total intake of both dioxins + dioxin-like PCBs and non-dioxin-like PCBs is fairly uniformly distributed over the foods consumed: meat products (23% and 27%, respectively), dairy products (27% and 17%, respectively), fish (16% and 26%, respectively), eggs (4% and 5%, respectively), vegetable products (13% and 7%, respectively), and industrial oils and fats (17% and 18%, respectively). Compared with earlier intake estimations the present estimation shows a continued reduction in the intake of dioxins as well as PCBs. This reduction is related to the decrease in the concentration of these substances in the majority of foodstuffs. Nevertheless, a small part of the population still has a rather high life-long averaged intake: 8% of the population is exposed to intake levels above the tolerable weekly intake for dioxins and dioxin-like PCBs of 14 pg WHO-TEQ per kg bw per week, as recently derived by the Scientific Committee on Food of the European Commission. For the non-dioxin-like PCBs an internationally accepted maximum intake level is still lacking. However, to provide risk managers with a health-based guideline to prevent health effects of exposure to non-dioxin-like PCBs, the (international) derivation of a tolerable daily intake is recommended. Monitoring the dietary intake of PCBs is just as important as monitoring the intake of dioxins and dioxin-like PCBs, and attempts to decrease the exposure to both compound classes need continuous attention.     

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.     

Levels of polychlorinated biphenyls (PCBs) in human adipose tissue from Baghdad/Iraq

The levels of 12 polychlorinated biphenyls (PCBs) in human adipose tissue samples gathered from patients, from three different hospitals, in Bagdad/Iraq were analyzed. All samples were extracted, cleaned up, and analyzed by GC/MS for dioxin-like PCBs. The total mean concentration of PCBs in all human adipose tissues samples was 404?μg/kg. Pentachlorobiphenyls were the predominant PCB congeners, accounting for 62.56% of the total PCB concentration found in the human adipose tissue samples which represent the most toxic compounds between all dioxin-like PCB congeners. The toxicity equivalents (TEQ PCBs) in all human adipose tissue samples were found in the range of 0.0126–86.284?μg TEQ/kg. The present average TEQ of 11.52?μg/kg is within the range that obtained by other studies.