Exp Neurobiol 2012; 21(1): 30-36
Published online March 31, 2012
© The Korean Society for Brain and Neural Sciences
Youngrok Do and Dong Kuck Lee*
Department of Neurology, Catholic University of Daegu School of Medicine, Daegu 705-718, Korea
Correspondence to: *To whom correspondence should be addressed.
TEL: 82-53-650-4267, FAX: 82-53-654-9786
Polychlorinated biphenyls (PCBs) are accumulated in our body through food chain and cause a variety of adverse health effects including neurotoxicities such as cognitive deficits and motor dysfunction. In particular, neonates are considered as a high risk group for the neurotoxicity of PCBs exposure. The present study attempted to analyze the structure-activity relationship among PCB congeners and the mechanism of PCBs-induced neurotoxicity. We measured total protein kinase C (PKC) activities, PKC isoforms, reactive oxygen species (ROS), and induction of neurogranin (RC-3) and growth associated protein-43 (GAP-43) mRNA in cerebellar granule cells of neonatal rats with phorbol 12, 13-dibutyrate ([3H]PDBu) binding assay, western blot, ROS assay, and reverse transcription PCR (RT-PCR) analysis respectively following the different structural PCBs exposure. Only non-coplanar PCBs showed a significant increase of total PKC-α and βII activity as measured with [3H]PDBu binding assay. ROS were more increased with non-coplanar PCBs than coplanar PCBs. The mRNA levels of RC-3 and GAP-43 were more induced with non-coplanar PCBs than coplanar PCBs, indicating that these factors may be useful biomarkers for differentiating non-coplanar PCBs from coplanar PCBs. Non-coplanar PCBs may be more potent neurotoxic congeners than coplanar PCBs. This study provides evidences that non-coplanar PCBs, which have been neglected in the risk assessment processes, should be added in the future to improve the quality and accuracy of risk assessment on the neuroendocrinal adverse effects of PCBs exposures.
Keywords: neurotoxicity syndrome, polychlorinated biphenyls, structure-activity relationship, protein kinase C, reactive oxygen
species, Nerve growth factor
Polychlorinated biphenyls (PCBs) are typical aromatic environmental pollutants that are accumulated through the food chain, prevail around us, and can possibly harm the human body. PCBs, which have been used widely as industrial materials for the past decades, also cause environmental pollution on a continuous basis through industrial products have been generated in the past . PCBs are characterized by carcinogenicity, reproductive toxicity, and immunotoxicity and have recently been known to disrupt neurotransmitters [2-4]. In animal testing, PCBs, which disrupt control of neurotransmitters and thyroid hormone in the brain, hinder normal brain development and exert effects on intellectual developments, such as behavior, cognition, and memory. These effects are known to be more serious especially in the brain of fetuses or infants where neuronal cells are developing actively .
PCBs have 209 theoretical congeners, the chemical structures of which can make differences to toxicities; therefore, toxic actions based on the structures are important in assessing their toxicities. Since dioxin and dioxin-like compounds are known to make diverse toxic actions via the medium of an aryl hydrocarbon (Ah) receptor, the Toxic Equivalent Factor (TEF), which assesses toxicity on the basis of reaction to an Ah receptor, has been introduced to the concept of toxicity assessment . PCBs are divided into coplanar (dioxin-like) PCBs reacting to an Ah receptor and non-coplanar (non-dioxin-like) PCBs with no affinity to an Ah receptor. The former has a similar structure to dioxin and makes similar toxic actions to dioxin while the latter tends to be neglected in risk assessment since it has shown no remarkable action mechanism or serious toxicity. However, the results of animal testing show that when Aroclor 1256 with both coplanar and non-coplanar structures is administered non-coplanar structure is mostly accumulated in the brain . Since non-coplanar PCBs have greater effects on the changes in neural development in brain cells than coplanar PCBs, many researches are being conducted on neurotoxicities of non-coplanar PCBs . As non-coplanar PCBs have recently been known to have no reaction to an Ah receptor but be sensitive to the secondary signaling system and neurotransmitters of the brain, be detected most frequently in breast milk, and be able to affect intellectual and behavioral development of young children, it is necessary to introduce a new concept of risk assessment .
Non-coplanar PCBs are known to activate protein kinase C (PKC) in cerebellar granule cells. PKC has 11 congeners or more, which vary in their intracellular distribution or action. While PKC-α and PKC-ε were shown to be target substances for 2,2'-dichlorobiphenyl , it is not known what PKC congeners are targets for PCB congeners and how their intracellular distribution varies.
It is known that PCBs decrease thyroid hormone (T4) of the brain in the growth period and that the decrease in thyroid hormone of the brain is closely related to oxidative stress . Dioxin-like compounds greatly increase cytochrome p450 (CYP1A1, 1A2) via an Ah receptor. This increase in metabolic enzyme forms reactive-oxygen metabolites and causes oxidant stress . As an important signal to cause such phenomena as apoptosis, the oxidative stress is also known to affect the cell cycle and have association with hypothyroidism in the growth-phase brain. So while oxidative stress may be a main action mechanism of PCBs-induced neuroendocrine disruption, there has been no research on this issue.
Neurotoxicity related to neuroendocrine disruption is getting much attention as a new feature of PCBs [8, 11]. PCBs neurotoxicities related to the neuroendocrine system cause changing of signaling pathway, hindrance to dopamine and serotonin synthesis, and decreased thyroid hormone in the growth-phase brain. Among them, the decrease in thyroid hormone is a typical phenomenon, which can transform neurofilament present within neuronal cells and prevent normal cell growth. In particular, thyroid hormone plays an important role in extracellular matrices, such as myelin-associated glycoprotein, Tenescin-C, GAP (growth associated protein)-43, and fibronectin, which are involved in neuronal cell migration and development [12-14]. Thyroid hormone is also known to control PKC activity through neurogranin (RC-3), which is a PKC matrix present in the brain alone . However, relations between many types of PCBs and extracellular matrices are rarely researched.
This study aims to analyze a neural action mechanism for different structural PCBs affecting growth and development of neuronal cells and control of neuroendocrine hormone in order to help the understanding of the effects of PCBs on neurotoxicity. An attempt is also made to help efficient risk assessment of PCBs and provide basic data to assess neurotoxicity more efficiently via developing a biomarker sensitive to the structural features.
This study used Polychlorinated biphenyls (PCBs) produced by AccuStandard (New Haven, CT, USA) and other essential reagents produced by Sigma-Aldrich (St. Louis, MO, USA). Reagents related to cell culture, including Dulbecco's modified Eagle's medium (DMEM), were purchased from Gibco BRL (Gaithersburg, MD, USA), and those related to assessment of reactive oxygen species from Promega (Madison, WI, USA). The following PCB congeners were selected to make a relative comparison between coplanar and non-coplanar structures: 3,3',4,4',5-Penta-CB (PCB 126), 3,3',4,4',5,5'-Hexa-CB (PCB 169), 2,2'-Di-CB (PCB 4), and Aroclor 1256.
0.1 µM to 200 µM PCBs were exposed for 24 hours to measure LDH, showing significant neurotoxicity at only 200 µM (Fig. 1). On the basis of this result, therefore, the contents showing no neurotoxicity-0.1, 1, 25, and 50 µM-were set for experimental exposure.
When general activity of PKC was analyzed using [3H]PDBu, non-coplanar PCBs were found to be more active than coplanar PCBs (Table 2). While PCB 126 and PCB 169 in the coplanar structure showed no remarkable change even at 50 µM, PCB 4 in the non-coplanar structure had binding increased by approximately 1.5 times. The commercial mixture containing a large amount of non-coplanar PCBs, Aroclor 1256, also showed the same level of increase in binding to PCB 4. It was therefore suggested that PCB causing PKC activity within neuronal cells had a significant non-coplanar structure. When PKC congeners playing an important role for the signaling system were analyzed with western blot, PKC-α made no apparent migration in PCB 126 or PCB 169 but made apparent migration from cytosol to membrane in PCB 4 and Aroclor 1256 (Fig. 2A). Similar observations were made from PKC-βII (Fig. 2B).
In terms of involvement of PCBs in ROS generation for neuronal cells, PCBs in the coplanar structure, such as PCB 126 and PCB 169, increased ROS generation by 1.3 times while PCB 4 and Aroclor 1256 increased it by 1.7 times. While both PCB structures were involved in ROS generation, non-coplanar PCBs generated more ROS (Fig. 3A). When making a comparison between treatment with mercury chloride alone and co-treatment with PCBs, the former increased it by 1.2 times while co-treatment with both coplanar and non-coplanar PCBs synergistically increased ROS generation (Fig. 3B). But only marginal statistical significances were observed in the ROS generation tests.
When extracellular matrices related to neuroendocrine hormone control disorders were analyzed using RT-PCR, mRNA of RC-3 showed no change in PCB 126 or PCB 169 but increased in non-coplanar PCBs, such as PCB 4 and Aroclor 1256, suggesting that a structure-activity relationship existed (Fig. 4A). The mRNA of GAP-43 increased in non-coplanar PCBs, such as PCB 4 and Aroclor 1256 but showed no increase in coplanar PCBs (Fig. 4B). But only marginal statistical significances were observed in the tests using growth factors.
PCBs disrupt control of neuroendocrine systems, such as thyroid hormone (T4), serotonin, and dopamine in the brain, and also exert effects on the secondary messenger related to the signaling pathway in the nervous system. A typical example of disruption in the neuroendocrine systems by PCBs is a decrease in thyroid hormone, which is known to control PKC activity through RC-3 which is the PKC matrix present in the brain alone , and the decrease in thyroid hormone is known to be closely related to activity of PKC . PKC also plays an important role in main action mechanisms of the neurotoxic symptoms of PCBs such as motor dysfunction and decreased learning ability and memory. The cerebellum was used as the target area for experiment since the neurotoxicities of PCBs are closely related to the cerebellum. Since the brain of newborn babies at the active growth phase is especially sensitive to the effect of neurotoxicity, this study used a 7-day-old cerebellar granule cell at the active growth phase as an experimental model.
In terms of [3H]PDBu binding, which means PKC migration to membrane for binding, non-coplanar PCBs were more influential on PKC activation than coplanar PCBs. It was therefore suggested that there was structure-activity relationship in the PKC-related signaling pathway. Dependence of an Ah receptor is important in establishing basis for comparison risk assessment of neurotoxicity of environmental pollutants with the existing Equivalency Factor (TEF) value. Therefore, the different effects based on the structure alone in this study may be very useful in predicting possibility of neurotoxicity.
As for PCBs-induced PKC activity using western blot, PKC-α and βII were higher than other PKC congeners, therefore they may be usable as indicators of the neurotoxic effects according to the PCBs structure. They can also give an opportunity to discover target substances of PCBs, possibly contributing to the understanding of mechanism of the signaling pathway in the PCBs-related neurotoxicity.
In the ROS assay, non-coplanar PCBs increased ROS generation more than coplanar PCBs. This implies that damage to neuronal cells by PCBs was related to structure-activity. There were greater increases in ROS generations with mercury chloride regardless of the PCBs structure. So there is more damage to the nervous system caused by PCBs exposure when the existing neurotoxic substances are present. This implies that as for daily exposure to PCBs via industrial products, intake of foods possibly high in mercury, such as tuna and shark, can increase damage to the nervous system.
RC-3 and GAP-43 play an important role in controlling intracellular calcium concentration and are also closely related to PKC activity. When PCBs-induced changes of RC-3 and GAP-43 were analyzed using RT-PCR, non-coplanar PCBs increased RC-3 and GAP-43 while coplanar PCBs made no significant change. These results are assumed not to be mediated by an Ah receptor but to be involved in a specific action mechanism of non-coplanar PCBs. The fact that the increase in GAP-43 is irrelevant to an Ah receptor implies that GAP-43 is playing a specific role in non-coplanar PCBs-induced PKC activity and intracellular calcium concentration. Therefore, any change in growth-related factors, such as RC-3 and GAP-43, in the growth-phase brain cells may be used as an indicator determining coplanar and non-coplanar structure-activity relationship in PCB mixture.
This study obtained the cerebellar granule cells from a 7-day-old SD rat and secured a technique for isolating, purifying, and culturing over 90% pure neurons to study an intracellular mechanism for many compounds related to neurotoxicity. This study also obtained a growth-phase brain cell model to screen neurotoxic substances to which the cells were vulnerable in the growth period. PCBs-induced neurotoxic mechanism for the fetus or infant group has been rarely known. This study indicate that non-coplanar PCBs were an important neurotoxic substance in the brain cells by exerting greater effects on PKC activity and neuronal cell growth factors in the growth-phase cerebellar cells than coplanar PCBs.
The results from this study can provide the base for screening coplanar and non-coplanar structures among PCB mixtures present in environment or foods. They are also assumed to be usable in understanding and distinguishing neurotoxic mechanisms of other similar environmental pollutants this study didn't deal with. The results will help securing structure-activity relationship (SAR) of PCBs, efficiently screening neuroendocrine disrupting factors present in foods or environment, and contributing to improvement in efficiency of risk assessment.
Table 1. Experimental conditions of reverse transcription-polymerase chain reaction (RT-PCR) analysis.
aInterleukin-1; bInterleukin-6; cTumor necrosis factor-α; dGlyceraldehyde-3-phosphate dehydrogenase..
Table 2. [3H] phorbol-12,13-dibutyrate (PDBu) binding following the exposure of substances (percentage of control).
While PCB 126 and PCB 169 in the coplanar structure showed no remarkable change even at 50 µM, PCB 4 and Aroclor 1256 in the non-coplanar structure had binding increased by approximately 1.5 times..