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Benzo(a)pyrene (B(a)P) is a mutagenic polycyclic aromatic hydrocarbon (PAH) commonly released into the environment. B(a)P induces phase I biotransformation metabolism and peroxisome proliferation which is characterised in rodents by increased peroxisomal volume density, accompanied by the transcriptional induction of peroxisomal proteins. The aim of the present work was to study peroxisome proliferation at the transcriptional level, in comparison to the transcription of the well-characterised cytochrome P450 1A gene (cyp1a) in the thicklip grey mullet Chelon labrosus. For this purpose, genes coding for the major peroxisomal membrane protein PMP70 and CYP1A were cloned using degenerate primers. Then juvenile mullets were single injected with B(a)P (5mg/kg) and transcription of palmitoyl-CoA oxidase (aox1), multifunctional protein (mfp1), 3-ketoacyl-CoA thiolase (thio), Delta(2),Delta(4)dienoyl-CoA reductase 2, pmp70, catalase and cyp1a was semi-quantified in liver and gills 1 and 7days after the injection. Transcription of aox1 and cyp1a was induced in gills 1day after B(a)P injection. Cyp1a transcription was also induced in mullet liver one day after injection, indicating that B(a)P was available for the liver. This was further proved by the significant accumulation of B(a)P-like metabolites in bile 7days after the injection. In liver, aox1, mfp1 and thio transcription was induced at day 1 followed by the induction of catalase transcription at day 7 that may reflect a response to an oxidative stress caused by B(a)P itself or by oxyradicals produced through the biotransformation metabolism and the peroxisomal beta-oxidation. These hepatic responses were not reflected at AOX1 activity level. In conclusion, it has been shown for the first time that the three enzymes in the fish peroxisomal beta-oxidation pathway are transcriptionally induced by B(a)P. It remains to be tested whether this enhanced transcription is reflected in an increase in the volume of peroxisomes.

Peroxisomal proteomics was applied to assess possible biological effects after the Prestige's oil spill. Mussels were sampled in July 2004 and 2005 in four stations in the NW (closest to the spill) and NE coasts of the Iberian Peninsula. Principal components analysis (PCA) suggested differences in protein expression among stations and sampling years. Several proteins were putatively identified by mass spectrometry and immunolocalization. PC1 separated the NW stations in 2004 from the rest of the stations and sampling years mainly due to up-regulation of peroxisomal beta-oxidation proteins and PMP70. PC3 separated the NE stations, based on up-regulation of the antioxidant enzyme catalase in 2004 compared to 2005. PC4 separated the stations in the NE and the NW. This work shows that environmental proteomics, together with multivariate data analysis, could provide information to interpret the effects of oil spills at cellular level in mussels.

Aquatic organisms living in coastal/estuarine areas show peroxisome proliferation after exposure to different environmentally relevant pollutants. In order to generate new tools to assess peroxisome proliferation in aquatic animals, peroxisomal enzymes were cloned using degenerate primers in the mussel Mytilus galloprovincialis and in the thicklip grey mullet Chelon labrosus. Fragments of catalase (CAT), thiolase (THIO), polyamine oxidase (POX) and xanthine oxidoreductase (XOR) were cloned and their expression pattern studied in different tissues by semi-quantitative RT-PCR. In mussels, CAT, THIO, POX and XOR were expressed in digestive gland, mantle and gills while in mullets CAT, THIO and POX were expressed in liver, spleen, brain, heart, muscle and gills. XOR was mainly expressed in liver and heart. Mature mullets showed the highest expression of peroxisomal enzymes in liver, spleen and brain, while in juveniles expression was mainly found in muscle tissues, liver and gills. Laboratory experiments of exposure to organic pollutants are being performed to study the usefulness of these tools to study peroxisome proliferation in pollution biomonitoring programmes.

Peroxisome proliferation has been proposed as novel biomarker of exposure to organic pollutants in aquatic organisms. Peroxisome proliferator compounds comprise a heterogeneous group of substances known for their ability to cause massive proliferation of peroxisomes and liver carcinogenesis in sensitive species such as rodents. Recently, several marine organisms (mussels and fish) have been shown as target species of peroxisome proliferators. In the present work, we aimed to investigate the specificity of the peroxisome proliferation response in mussels. For this purpose, mussels (Mytilus edulis) were exposed for three weeks to North Sea crude oil (NSO), a mixture of NSO, alkylphenols and extra PAHs (MIX), diallylphthalate (DAP), bisphenol-A (BPA) and tetrabromodiphenylether (TBDE), or transplanted for three weeks to four stations showing different copper concentrations in a copper mine. Peroxisome proliferation was assessed by measuring the activity of the peroxisomal beta-oxidation enzyme acyl-CoA oxidase (AOX) and the volume density occupied by peroxisomes (V(VP)) in the digestive gland. Mussels exposed to NSO and MIX showed significantly increased AOX activities and V(VP) compared to control animals. Significantly higher V(VP) was also found in DAP and TBDE exposed mussels. V(VP) did not vary in mussels transplanted into a copper concentration gradient. Our results confirm the usefulness and specificity of peroxisome proliferation as a suitable biomarker of exposure to organic contaminants such as oil derived hydrocarbons, phthalate plasticizers and polybrominated flame retardants in mussels.

We aimed to determine the effects of changes in polycyclic aromatic hydrocarbon (PAH) and polychlorinated biphenyl (PCB) bioavailability on peroxisome proliferation and antioxidant enzymes to assess their potential use as pollution biomarkers. For this, mussels (Mytilus galloprovincialis) were sampled in Txatxarramendi and transplanted to Arriluze, Muskiz, and Plentzia (northern Spain), and vice versa. Arriluze was the most heavily polluted site, followed by Plentzia, Txatxarramendi, and Muskiz. Animals transplanted from a polluted station to a cleaner station lost contaminant load in three to six weeks, and when transplanted to a more polluted station, they accumulated PAHs and PCBs accordingly. Peroxisomal acyl-A oxidase (AOX) activity was the highest in animals from Arriluze, and animals transplanted to Arriluze showed increased AOX activity, reaching the levels of native mussels. Mussels from Txatxarramendi showed the lowest peroxisomal volume density (Vvp). Among mussels from Txatxarramendi, only those transplanted to Plentzia showed increased Vvp, whereas animals from Arriluze and Muskiz transplanted to Txatxarramendi after 2 d and six weeks, respectively, had decreased Vvp. Two days after transplant, superoxide dismutase and glutathione peroxidase activities were significantly lower in mussels from Arriluze and Muskiz, respectively, than in those from Txatxarramendi and than in animals transplanted to Txatxarramendi from these stations. In conclusion, transplant experiments with mussels are useful to assess the effects of pollution. Peroxisome proliferation, measured as induction of AOX or increased Vvp, shows great potential as a biomarker of pollution to be included in pollution monitoring programs. In the present work, we have demonstrated that peroxisome proliferation is a reversible phenomenon in mussels.

Environmental estrogenic compounds or xenoestrogens can mimic natural estrogens and cause a variety of adverse effects on aquatic wildlife. The purpose of the present work was to investigate if xenoestrogens are able to cause proliferation of liver peroxisomes using zebrafish (Danio rerio) as a model. Adult male zebrafish were exposed for 15 days to 17beta-estradiol (E2) and the xenoestrogens dibutylphthalate (DBP), methoxychlor (MXC), 4-tert-octylphenol (OP) and 17alpha-ethynylestradiol (EE2). All five tested compounds caused significant proliferation of liver peroxisomes (p < 0.05) as indicated by increased peroxisomal surface and numerical densities and elevated activities of the peroxisomal beta-oxidation enzyme acyl-CoA oxidase (AOX). In the case of DBP, MXC and E2, positive significant correlations between peroxisomal density parameters and AOX were found. The treatments did not produce gross alterations in testis histology, but spermatogenic cell proliferation was disturbed in E2 and EE2-treated groups and vitellogenin levels increased significantly in fish exposed to MXC, OP, EE2 and E2 with respect to controls. Furthermore, a significant correlation between vitellogenin levels and AOX activity was found for MXC, OP and EE2 treatments, suggesting that for the latter xenoestrogens early estrogenic effects are associated with liver peroxisome proliferation. No such association occurred with typical peroxisome proliferators such as DBP.

With the aim of studying levels of antioxidant and peroxisomal enzymes and the structure of peroxisomes in relation to body burdens of polycyclic aromatic hydrocarbons (PAHs) and polychlorinated biphenyls (PCBs), mussels Mytilus galloprovincialis, oysters Crassostrea sp., crabs Carcinus maenas and mullets Mugil cephalus were sampled in two Basque estuaries (Bay of Biscay): Urdaibai (Laida, Txatxarramendi, Arteaga, and downstream a sewage treatment plant-STP) and Plentzia. In general, animals showed higher concentrations of contaminants in winter than in summer and no relevant differences were detected among locations. Conversely, antioxidant enzyme activities were higher in summer. Enzyme expression was studied in mullets using immunochemical methods. By immunoblotting season-dependent differences were detected for Mn-superoxide dismutase (Mn-SOD). As for the immunohistochemical staining, mullets sampled in summer in Plentzia showed significantly higher optical densities for acyl-CoA oxidase and lower for both Cu,Zn-SOD and Mn-SOD than those collected downstream a STP as well as higher catalase immunostaining than those collected in winter. Peroxisomal volume density (V(vp)) of mussels sampled in Laida and Txatxarramendi did not show seasonal variations, while for oysters collected in Laida and Arteaga V(vp) was higher in summer. Crab and mullet V(vp) were also higher in summer. In conclusion, the estuaries of Urdaibai and Plentzia can be considered as low to moderately polluted areas and levels of PAHs and PCBs do not show marked variations apart from seasonal variations. Animals can be adapted to low pollution conditions and, under these circumstances, seasonal factors might affect biomarker responses to a greater extent than pollution variations.

Exposure of marine animals to certain organic and metal pollutants is thought to enhance reactive oxygen species (ROS) production with concomitant alterations of antioxidant defence mechanisms. Some of these organic pollutants cause peroxisome proliferation, a process resulting also in possible enhanced production of ROS. The aim of this study was to investigate the effects of two organic xenobiotics, benzo(a)pyrene (B(a)P) and di(2-ethylhexyl)phthalate (DEHP), as well as the effects of cadmium (Cd), on antioxidant and peroxisomal enzymes and on peroxisomal volume density in the digestive gland of mussel, Mytilus galloprovincialis Lmk., experimentally exposed for 21 days. Special attention was paid to the interactive effects of organic and metal compounds by exposing one group of mussels to a mixture of B(a)P and Cd. Exposure of mussels to Cd caused a decrease in superoxide dismutase (SOD) activity, in Mn-SOD protein levels and in volume density of peroxisomes. B(a)P exposure significantly increased catalase and glutathione peroxidase (GPX) and inhibited Mn-SOD after 21 days of exposure. B(a)P also caused a slight increase in acyl-CoA oxidase (AOX) activity and peroxisomal volume density after 21 days of exposure. Cd tended to inhibit changes provoked by B(a)P, indicating that responses to organic xenobiotics can be modulated by concomitant exposure to metal contaminants. Exposure to DEHP increased catalase and AOX and inhibited SOD activity and Mn-SOD protein levels. In conclusion, peroxisome proliferation, measured as an increase of the peroxisomal enzymes catalase and AOX (up to 1.53-fold for AOX), is a specific response to organic contaminants such as B(a)P and DEHP, whereas Cd does not cause peroxisome proliferation. Thus, peroxisome proliferation may be a specific biomarker of organic pollutants in mussels. Both organic and metal pollutants inhibited SOD activity and protein levels (up to 0.21-fold for Mn-SOD protein levels), the latter offering potential as general marker of pollution.

Abstract: Due to the ability to respond after exposure to organic toxic compounds, peroxisome proliferation is used as biomarker of exposure to organic pollutants in mussels and in fish. Mussels are worldwide studied as sentinels of pollution in marine environments while mullets such as the thicklip grey mullet Chelon labrosus have been proposed as appropriate sentinel species since they inhabit highly polluted environments. In order to study genes of the inducible peroxisomal β-oxidation pathway in mussels Mytilus galloprovincialis and in C. labrosus, genes coding for the three enzymes in the inducible peroxisomal β-oxidation pathway, palmitoyl-CoA oxidase (AOX1), multifunctional protein (MFP1 in mullet and MFP2 in mussels), and 3-ketoacyl-CoA thiolase (THIO), were cloned. Additionally, a fragment of the peroxisomal Δ2, Δ4 dienoyl-CoA reductase 2 (DECR) necessary for the β-oxidation of unsaturated fatty acids was cloned in mullets. The whole open reading frame of aox1 sequenced in both mussels and mullets revealed high homology with known aox1 sequences, with highly conserved important domains such as the FAD binding motif or the typical peroxisomal targeting signal (PTS1). A thorough in silico analysis of the gene and genome databases allowed to identify in fish and molluscs sequence homologs of all the enzymes necessary for 2 of the 3 different paralog peroxisomal β-oxidation pathways described in metazoans (AOX1, AOX3, MFP1, MFP2, THIO and sterol carrier protein X). Only the enzyme necessary for the oxidation of branched chain fatty acids, AOX2, described in mammalian, avian and amphibian species, seems to be lacking from the genomes of fish and molluscs. In order to study the expression and regulation capacity of peroxisomal β-oxidation genes, aox1 and thio expression was determined in different tissues of mature and immature mullets and mussels collected in January and June, both genes being expressed higher in the digestive gland of mussels collected in June compared to January. Finally, in silico studies of the promoter regions in the piscine genomes available in the Ensembl genome repository, allowed the identification of putative peroxisome proliferator response elements that could explain the possible cellular and molecular mechanisms leading to peroxisome proliferation in fish. Further studies are needed to decipher molecular mechanisms of peroxisome proliferation in aquatic organisms under exposure to peroxisome proliferator xenobiotics. [Copyright &y& Elsevier]

With the aim of assessing the biological effects of pollution along three gradients of pollution in the NW Mediterranean Sea, a biomonitoring survey was implemented using a battery of biomarkers (lysosomal membrane stability, lysosomal structural changes, metallothionein (MT) induction and peroxisome proliferation) in mussels over a period of two years as part of the EU-funded BEEP project. Mussels from the most impacted zones (Fos, Genova and Barcelona harbours) showed enlarged lysosomes accompanied by reduced labilisation period of lysosomal membranes, indicating disturbed health. MT levels did not reveal significant differences between stations and were significantly correlated with gonad index, suggesting that they were influenced by gamete development. Peroxisomal acyl-CoA oxidase (AOX) activity was significantly inhibited in polluted stations possibly due to interactions among mixtures of pollutants. In conclusion, the application of a battery of effect and exposure biomarkers provided relevant data for the assessment of biological effects of environmental pollution along the NW Mediterranean Sea. [Copyright &y& Elsevier]

The aim of the present work was to study the effects of the peroxisome proliferator dibutylphthalate (DBP) and the xenoestrogen 17α-ethynylestradiol (EE2) on liver peroxisomes, reproduction, and development of zebrafish (Danio rerio). In experiment 1, newly fertilized zebrafish eggs were exposed for five weeks, covering the entire period of sexual determination, to nominal concentrations of 25 and 100 μg/L of DBP and 5 μg/L of EE2. In experiment 2, adult female zebrafish were exposed for 15 d to 100 and 500 μg/L of DBP and 5 μg/L of EE2, and afterward, they were paired with untreated males to study the effects in the resultant offspring. Ethynylestradiol provoked marked mortality (∼50%) and delayed development of larvae as well as sterility of adult females, possibly related to alterations in aromatase gene expression. Ethynylestradiol up-regulated vitellogenin expression in the early life stages and increased vitellogenin synthesis and accumulation in adult females. Ethynylestradiol caused liver peroxisome proliferation in early life stages but not in adult females. Dibutylphthalate caused teratogenic effects in early life stages and mortality of the larvae obtained from exposed females. Dibutylphthalate provoked liver peroxisome proliferation and up-regulation of cytochrome P450A1 in early life stages at the end of the exposure and in adult females. Dibutylphthalate also up-regulated the expression of aromatase genes. In conclusion, the xenoestrogen EE2 caused liver peroxisome proliferation in early life stages of zebrafish, but the peroxisome proliferator DBP did not behave as a typical xenoestrogen. Overall, changes in gene expression were more marked during early life stages than in adult female zebrafish. [ABSTRACT FROM AUTHOR]

Peroxisomes increase in size and number in responsive animals ranging from mammals to marine mussels and fish species when treated with certain compounds named peroxisome proliferators. This phenomenon, known as peroxisome proliferation, is mediated by nuclear receptors termed peroxisome proliferator-activated receptors (PPARs). Three PPAR subtypes have been described (α, β, and γ) and in mammals PPARα is mainly expressed in tissues that catabolize fatty acids, PPARβ is ubiquitously distributed, and PPARγ is mainly expressed in the adipose tissue and immune system. The aim of this study was to analyze the tissue distribution of different PPAR subtypes in zebrafish Danio rerio using commercially available antibodies against PPARα, PPARβ, and PPARγ. In western blots, specific bands were detected at about 58 kDa for PPARα and PPARβ. For PPARγ the band was detected at 56 kDa. Similar results were obtained in mouse liver homogenates used as positive control, indicating the specificity of the antibodies. Immunohistochemistry was performed in paraformaldehyde-fixed tissue using either microwave or microwave plus trypsin pretreatment for antigen retrieval. In zebrafish, PPARα was expressed mainly in liver parenchymal cells, proximal tubules of kidney, enterocytes, and pancreas. PPARβ showed a widespread distribution and was expressed in the liver, proximal and distal tubules and glomeruli of the kidney, pancreas, enterocytes and smooth muscle of the intestine, skin epithelium, lymphocytes, and male and female gonads. PPARγ expression was weak in pancreatic cells, intestine, and gonads for both pretreatments. Most of the signal detected was cytoplasmic; only in the cases of PPARα and PPARβ was some nuclear labeling detected in the liver. In mouse tissues, the distribution of PPAR subtypes was similar to that described previously for rats. Our results demonstrate that all three distinct PPAR subtypes are present in zebrafish. The tissue and cellular distribution of PPAR subtypes in zebrafish resembled partly that described before in mammals. Further studies are needed to decipher the functions of PPAR subtypes in zebrafish and other aquatic organisms and particularly their role in regulation of metabolic responses to xenobiotic exposure. [ABSTRACT FROM AUTHOR]

The aim of this work was to determine the immunolocalization of the antioxidant enzymes catalase, Cu,Zn-superoxide dismutase (SOD), Mn-SOD, and glutathione peroxidase (GPX) in the bivalve mollusks Mytilus galloprovincialis and Crassostrea sp., the crab Carcinus maenas, and the teleostean fish Mugil cephalus. By immunoblotting, crossreactivity between antibodies and the corresponding proteins in the digestive gland/hepatopancreas of invertebrates and the fish liver was demonstrated. Immunohistochemical studies showed that the stomach epithelium was strongly immunostained for catalase in mollusks. In crabs, ducts showed stronger immunostaining than tubules and in mullet hepatocytes the reaction appeared in discrete granules corresponding to peroxisomes. With regard to Cu,Zn-SOD, the apex of the tubule cells in mussels and crabs was distinctly immunostained, whereas in oysters the reaction was more marked in ducts and in mullet liver a uniform diffuse cytoplasmic staining was found. Mn-SOD was strongly positive in mollusk and crab ducts and in mullet periportal hepatocytes. Finally, GPX was not detected in mussels while in oysters a slight reaction was noted in all cell types. In crabs, connective tissue cells and the apex of duct cells were immunostained, but in mullet liver only erythrocytes appeared reactive. Immunoelectron microscopy revealed that catalase was localized in peroxisomes with a dense labeling in fish and less intense labeling in invertebrates. Cu,Zn-SOD was mainly a cytosolic protein although additional positive subcellular sites (peroxisomes, nuclei) were also observed, while Mn-SOD was restricted to mitochondria. GPX was localized in the cytosol, nucleus, and lysosomes, occurring also in peroxisomes of the fish liver. The results presented here provide a basis for future application of the immunodetection techniques to study the possible differential induction of antioxidant enzymes in aquatic organisms subjected to oxidative stress as a result of exposure to environmental pollutants. [ABSTRACT FROM AUTHOR]

Abstract: Aquatic organisms are exposed to diverse xenobiotics that cause peroxisome proliferation and/or endocrine disruption, both modulated in vertebrates by transcription factors of the nuclear receptor (NR) superfamily. Peroxisome proliferators are agonists of peroxisome proliferator-activated receptors (PPARs) that heterodimerize with the retinoid X receptor (RXR). Many xenoestrogens activate the estrogen receptor (ER). Here, 1090 bp of PPARα, 1255 bp of PPARγ, 278 bp of RXRα, and 578 bp of ERα of thicklip grey mullet Chelon labrosus were cloned. Sequences were highly conserved, although relevant changes with respect to mammalian homologs were identified in PPARγ and ERα. Semi-quantitative RT-PCR was used to determine if these NRs were expressed in different tissues of male, female and undifferentiated mullets captured in January and June. Expression of PPARs was highest in liver and lowest in muscle. RXRα expression was homogeneous excepting a low expression in male and female gill in January and brain and heart of undifferentiated fish in January and June. ERα expression predominated in liver and female gonad in June. The expression level of PPARs and ERα was significantly higher in liver in January than in gills in January or June. The present results show tissue-dependent modulation of expression of NRs in mullets. [Copyright &y& Elsevier]

Abstract: Aquatic organisms living in coastal and estuarine areas are exposed to diverse contaminants which can cause peroxisome proliferation. Peroxisome proliferators are agonists of peroxisome proliferator-activated receptors (PPARs), members of the nuclear receptor superfamily. We have recently demonstrated expression of the three PPAR isoforms in liver of mullet Chelon labrosus and other fish species by immunohistochemistry. The goal of the present study was first to clone PPARα and second to investigate its expression pattern in various tissues of mullet. PCR-based screening of mullet cDNA with PPARα specific degenerate primers resulted in amplification, subcloning and sequencing of a 1090bp cDNA fragment (AY618315) that encodes mullet PPARα and exhibits highest amino acid identity to fish Sparus aurata PPARα (90%). Semi-quantitative RT-PCR was used to characterize the expression of PPARα in brain, muscle, liver, spleen, gill, heart and female gonad of juvenile and adult male and female mullet. For this, mullet 18S-rRNA (AY825252), β-actin (AY836368) and elongation factor α (AY836369) were cloned and used as internal reference for RT-PCR. Expression of PPARα was detected in all tissues, was highest in liver and lowest in adult male and female muscle. [Copyright &y& Elsevier]

During the last decade, peroxisome proliferation has emerged as a novel biomarker of exposure to certain organic chemical pollutants in aquatic organisms. Peroxisome proliferation is mediated by nuclear receptors, peroxisome proliferator-activated receptors (PPARs). Three PPAR subtypes have been described in mammals: PPARα, PPARβ and PPARγ. PPARs have also been discovered in several fish species. The aim of the present study was to investigate the expression of PPAR subtypes and their cellular distribution patterns in the liver of gray mullet Mugil cephalus, a fish species widely distributed in estuaries and coastal areas in Europe and used as sentinel of environmental pollution. For this purpose, antibodies were generated against the three subtypes of mouse PPARs and different protocols of antigen retrieval were used. In western blots, main bands were detected of approximately 44 kDa for PPARα, two bands of 44 and 58 kDa for PPARβ and a single band of 56 kDa for PPARγ. Similar results were obtained in mouse liver and may indicate antibody recognition of two forms of the protein in certain cases. PPARα was the subtype most markedly expressed in gray mullet liver, being expressed mainly in melanomacrophages, nuclei of hepatocytes and sinusoidal cells and connective tissue surrounding bile ducts. PPARβ was expressed in the same cell types but immunolabeling was generally weaker than for PPARα. PPARγ showed very weak expression; positivity was mainly found in melanomacrophages and connective tissue surrounding bile ducts. Our results demonstrate that all the three PPAR subtypes are expressed in gray mullet liver but in different intensities. The cellular distribution patterns of PPAR subtypes in gray mullet liver resembled partly those found in mouse liver with PPARα as the main subtype expressed in hepatocytes. The fact that melanomacrophages, cells of the immune system in fish, show strong expression of both PPARα and PPARβ whereas PPARγ expression is almost restricted to this cell type suggest a significant role of PPAR-mediated regulation of cell function in melanomacrophages. [Copyright &y& Elsevier]