Non-coplanar polychlorinated biphenyls (PCBs) are direct agonists for the human pregnane-X receptor and constitutive androstane receptor, and activate target gene expression in a tissue-specific manner
Highlights
► Several Non-coplanar PCBs are able to directly activate both PXR and CAR in vitro. ► PCB153 is the most potent direct activator of PXR and CAR nuclear receptors. ► Non-coplanar PCB activation of CYP3A4/MDR1 reporter genes is structure-dependent. ► Non-coplanar PCB activate CYP3A4/MDR1 reporter genes in a tissue-dependent. ► PCB153 is the most potent activator of PXR/CAR target gene in all tissues.
Introduction
Polychlorinated biphenyls (PCBs) were historically used in a large number of industrial applications, including coolants, plasticisers, lubricants and insulators (Safe, 1984, Safe, 2001). Their high chemical stability has resulted in environmental persistence, and coupled with their highly lipophilic nature raises the potential for bioaccumulation in higher mammals, including humans.
There are 209 potential PCB congeners, of which 36 congeners are considered to be environmentally threatening due to environmental prevalence, bioaccumulation in animal tissues and known toxic effects (McFarland and Clarke, 1989). These congeners can be divided into non-ortho PCBs that have a coplanar configuration, and ortho‐substituted PCBs with a non-coplanar configuration. PCB congeners with zero or one ortho-chlorine substituent (e.g. PCB77) exhibit toxic effects similar to 2,3,7,8-tetrachlorodibenzo-p-dioxin (TCDD), and these are mediated through the aryl hydrocarbon receptor (AhR); thus, these PCBs are referred to as dioxin-like PCBs. These adverse effects include hepatotoxicity, elevated blood lipids, immune suppression, reproductive and developmental toxicity and carcinogenicity (Safe, 1984, Safe, 2001). Due to these highly undesirable properties, PCB manufacture was banned in the late 1970s and their usage severely restricted. However, due to the highly persistent nature of these chemicals, it is estimated that there remains over 750,000 tonnes of PCBs in the biosphere, and hence they still represent an important potential toxic contaminant.
Whilst the majority of risk assessment interest has focussed on the coplanar dioxin-like PCBs, non-coplanar PCBs are also highly environmentally prevalent, with PCB138, 153 and 180 being widely present in the environment and thus must also be included in any hazard/risk assessment (Safe, 1994). Non-coplanar PCBs (e.g. PCB153) possess ortho‐chlorine substituents on the biphenyl ring that twists the structure away from a single plane. This significantly reduces the affinity for AhR, and indeed these compounds are likely to act as inhibitors of AhR-mediated activation (Suh et al., 2003). Non-coplanar PCBs are more likely to act as ligands for members of the nuclear receptor family of transcription factors (Wu et al., 2009). This activity may be important considering that not all of the adverse effects associated with PCB exposure are mediated via AhR. For example, the hydroxylated metabolites of PCBs are weak oestrogen receptor agonists, as well as inhibitors of oestrogen sulphotransferase; as such, PCBs may have an endocrine disrupting effect, which may underlie their reproductive toxicity (Kester et al., 2000). Thus it is important to assess the hazard of non-coplanar PCBs to humans to inform a full risk assessment.
It has been suggested that non-coplanar PCBs may act as ligands for the constitutive andorstane receptor (CAR) and/or the pregnane‐X receptor (PXR) (Jacobs et al., 2005, Schuetz et al., 1998), and may thus activate CAR/PXR target genes expression. Due to this activity, this group of PCBs is often referred to as ‘Phenobarbital-like PCBs’.
There is thus a need to examine the non-AhR‐mediated effects of PCBs, and specifically the non-coplanar phenobarbital-like PBCs, for comprehensive risk assessments to be undertaken. As such, we have examined the ability of the non-coplanar PCBs PCB99, 138, 153, 180 and 194 to directly activate CAR and PXR, as well as their ability to activate target gene expression in liver, lung and intestinal cells in vitro.
Section snippets
Reagents
Fugene-6 transfection reagent was purchased from Roche Diagnostics, Lewes, UK. Unless otherwise stated all other chemicals were of molecular biology grade and obtained from Sigma-Aldrich (Poole, UK). The Huh7 human hepatocellular carcinoma cell line (Nakabayashi et al., 1982) was a kind gift from Dr Steve Hood (GSK, Ware, UK). Human intestinal (Caco2) and lung (A549) cell lines were purchased from ECACC (Porton Down, UK). All cells were routinely cultured in minimal essential medium with
Results
A range of PCB congeners were selected for study that encompassed the coplanar PCB77, and the non-coplanar PCB99, 138, 153, 180 and 194 (Fig. 1). Initially, we confirmed that only the coplanar PCB77 was able to activate AhR-mediated gene expression. Human liver, intestine and lung cell lines were exposed to each of the PCBs (10 μM) for 48 h and CYP1A1 transcript levels measured by Q-PCR. PCB77 elicited a significant increase in CYP1A1 transcript levels in all three cell lines; Caco2 cells were
Discussion
Previous data has provided indirect evidence for the interaction of non-coplanar PCBs with the nuclear receptors PCR and CAR. Using a reporter gene system, Tabb et al. (2004) were able to demonstrate that highly chlorinated, non-coplanar, PCBs were able to impact on PXR‐mediated transcription. Interestingly, they demonstrated that these highly chlorinated PCBs were able to activate reporter gene expression of target genes via mouse and rat PXR, but inhibited human PXR-mediated transcriptional
Conflict of interest
None.
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2022, Science of the Total EnvironmentCitation Excerpt :These compounds are also bioaccumulated and biomagnified in higher trophic animals through the food webs (Brown et al., 2018; Rigét et al., 2019; Tanabe et al., 2003; WHO, 2010). Many of these compounds bind intracellular receptors (Al-Salman and Plant, 2012; Salama et al., 2003; Sanders et al., 2005; Wahlang et al., 2016; Wall et al., 2015; Woolcott et al., 2001; Zhang et al., 2012) and cause endocrine disruption, reproductive failure, neurotoxicity, immunotoxicity, mutations, and cancer promotion (Alonso et al., 2010; Aoki, 2001; Jin et al., 2014; Lind and Lind, 2018; Yamamoto et al., 2005). Moreover, recent studies have shown that exposure to POPs are involved in the increase of type 2 diabetes and obesity (Ngwa et al., 2015; Taylor et al., 2013).