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Global gene expression associated with hepatocarcinogenesis in adult male mice induced by in utero arsenic exposure.

Our previous work has shown that exposure to inorganic arsenic in utero produces hepatocellular carcinoma (HCC) in adult male mice. To explore further the molecular mechanisms of transplacental arsenic hepatocarcinogenesis, we conducted a second arsenic transplacental carcinogenesis study and used a genomewide microarray in profile arsenic-induced aberrant gene expression more extensively. Briefly, pregnant C3H mice were given drinking water containing 85 ppm arsenic as sodium arsenite or unaltered water from days 8 to 18 of gestation. The incidence of HCC in adult male offspring was increased 4-fold and tumor multiplicity 3-fold after transplacental arsenic exposure. Samples of normal liver and liver tumors were taken at autopsy for genomic analysis. Arsenic exposure in utero resulted in significant alterations (p < 0.001) in the expression of 2,010 genes in arsenic-exposed liver samples and in the expression of 2,540 genes in arsenic-induced HCC. Ingenuity Pathway Analysis revealed that significant alterations in gene expression occurred in a number of biological networks, and Myc plays a critical role in one of the primary networks. Real-time reverse transcriptase-polymerase chain reaction and Western blot analysis of selected genes/ proteins showed > 90% concordance. Arsenic-altered gene expression included activation of oncogenes and HCC biomarkers, and increased expression of cell proliferation-related genes, stress proteins, and insulin-like growth factors and genes involved in cell-cell communications. Liver feminization was evidenced by increased expression of estrogen-linked genes and altered expression of genes that encode gender-related metabolic enzymes. These novel findings are in agreement with the biology and histology of arsenic-induced HCC, thereby indicating that multiple genetic events are associated with transplacental arsenic hepatocarcinogenesis. Key words: Agilent mouse oligo 22K microarray, arsenic, hepatocellular carcinoma, real-time RT-PCR, transplacental exposure, Western blotting. Environ Health Perspect 114:404-411 (2006). doi: 10.1289/ehp.8534 available via[Online 6 October 2005]


Inorganic arsenic is an environmental pollutant. Arsenic exposure in humans comes mainly from consumption of drinking water contaminated with inorganic arsenic [National Research Council (NRC) 1999], but elevated exposure can occur from burning of coal containing high levels of inorganic arsenic (Liu et al. 2002). Epidemiologic studies have demonstrated that chronic arsenic exposure causes tumors of the skin, urinary bladder, lung, liver, prostate, kidney, and possibly other sites [International Agency for Research on Cancer ([ARC) 1987; Morales et al. 2000; NRC 1999]. Until recently, inorganic arsenic was considered a "paradoxical" human carcinogen because of strong human evidence but limited evidence for animal carcinogenesis (IARC 1987; Waalkes et al. 2004a, 2004b). Indeed, negative results had been obtained for inorganic arsenic carcinogenesis in mice, rats, hamsters, rabbits, dogs, and monkeys (IARC 1987; Kitchin 2001). Recently, important advances have been made in the development of rodent models of inorganic arsenic carcinogenesis. These include skin cancer models in which inorganic arsenic acts as a co-promoter with 12-O-tetradecanoyl phorbol-13-acetate in Tg.AC mice (Germolec et al. 1998), or as a co-carcinogen with ultraviolet irradiation in hairless mice (Rossman et al. 2001). In addition, our group has developed a transplacental model in which short-term exposure to inorganic arsenic in utero produces a variety of internal tumors in the offspring when mice reach adulthood (Waalkes et al. 2003, 2004b). These tumors include cancers of the liver, lung, ovary, and adrenal induced in adulthood by transplacental exposure to arsenic (Waalkes et al. 2003, 2004b).

The brief period of exposure (10 days) to inorganic arsenic, which was sufficient for it to be a complete transplacental carcinogen in mice, is not only alarming but points to a clear period of high sensitivity to the metalloid. Indeed, gestation is a period of high sensitivity to chemical carcinogenesis in general in both rodents and probably humans (Anderson et al. 2000). Inorganic arsenic can readily cross the placenta and enter the fetal system (Chattopadhyay et al. 2002; Concha et al. 1998; NRC 1999). Thus, in human populations exposed to inorganic arsenic, it is reasonable to assume that exposure during gestation does occur, and that the carcinogenesis sensitivity observed in rodents may predict similar effects in humans.

Hepatocellular carcinoma (HCC) has been identified as a tumor type associated with arsenic exposure in humans (Centeno et al. 2002; Chen and Ahsan 2004; Chen et al. 1997; Zhou et al. 2002). HCC and nonalcoholic liver cirrhosis and ascites are leading causes of mortality in the arsenic endemic area of Guizhou, China (Liu et al. 2002; Zhou et al. 2002). Also, hepatomegaly and liver diseases are commonly associated with arsenic exposure through the drinking water in West Bengal, India (Santra et al. 2000). In accord with human data, transplacental exposure to inorganic arsenic in mice induced a marked, dose-related increase in HCC formation in male offspring in both an initial (Waalkes et al. 2003) and a subsequent followup study (Waalkes et al. 2004a, 2004b). In utero arsenic exposure also caused a variety of hepatic genes to be aberrantly expressed, including genes probably critical to the carcinogenic process, as evidenced by analysis of liver samples taken at autopsy during the initial transplacental study with sodium arsenite (Liu et al. 2004; Waalkes et al. 2004a). This initial genomic analysis was limited to individual genes of interest (Waalkes et al. 2004a) or to a limited number of genes (588) in a custom array (Liu et al. 2004).

Our second transplacental arsenic carcinogenesis study in mice (Waalkes et al. 2004b) confirmed the hepatocarcinogenic potential of gestational arsenic exposure seen in the initial study (Waalkes et al. 2003). It also provided a unique opportunity to perform a genomewide analysis through the National Center for Toxicogenomics using the Agilent 22K chip arrays. Changes in expression of specific genes of interest were confirmed by real-time reverse transcriptase-polymerase chain reaction (RT-PCR) and Western blot analysis. This study confirmed and extended our initial observations, but it also revealed a number of novel pathways and gene expression alterations potentially associated with hepatocarcinogenesis induced by transplacental arsenic exposure.

Materials and Methods

Chemicals. Sodium arsenite (NaAs[O.sub.2]) was obtained from Sigma Chemical Co. (St. Louis, MO) and dissolved in the drinking water at 85 mg arsenic/L (85 ppm). The Agilent 22K mouse oligo array was obtained from Agilent Technologies (Palo Alto, CA). Monoclonal antibodies against [alpha]-fetoprotein (sc-8399), K-ras (sc-30), c-myc (sc-42), estrogen receptor (ER)-[alpha] (sc-8002), [beta]-actin (sc-1616) and polyclonal antibodies against cyclin DI (sc-753), cdk4 (sc-601), and endothelial growth factor receptor (EGFR, sc-03) were obtained from Santa Cruz Biotechnology (Santa Cruz, CA). Monoclonal antibodies against proliferating cell nuclear antigen (PCNA, 610664), cytokeratin 5/8 (550505), and plasminogen activator inhibitor-1 (PAI-1, 612024) were purchased from BD Biosciences (San Jose, CA). All other chemicals were commercially available and of reagent grade.

Animal treatment and sample collection. We conducted the present study using liver tumors and nontumorous normal liver samples collected in the second of a series of transplacental arsenic carcinogenesis studies in mice for which pathological results have already been reported (Waalkes et al. 2004b). In this study timed pregnant C3H mice were given drinking water ad libitum containing 85 ppm arsenic as sodium arsenite or unaltered water from days 8-18 of gestation. Offspring were weaned at 4 weeks, then randomly placed into separate groups (n = 25 from 10 dams/group) according to maternal exposure level and observed for up to 104 weeks. Animal care was provided in accordance with the Guide on the Care and Use of Animals (Institute of Laboratory Animal Resources 1996), and the Institutional Animal Care and Use Committee approved the study proposal. Animals used in this study were treated humanely and with regard for the alleviation of suffering. Samples of large tumors, later confirmed as HCC, and normal surrounding liver tissues were taken at autopsy, snap frozen in liquid nitrogen, and compared with normal liver samples from contemporaneous controls. A total of 17 samples from male mice were analyzed, including 5 inorganic arsenic-induced HCC samples (designated As-HCC), 5 samples of surrounding nontumorous, normal liver tissues from arsenic-treated mice (As-Normal), and 7 samples of age-matched control mouse liver (Control).

Microarray analysis. We isolated total RNA from liver samples with TRIzol agent (Invitrogen, Carlsbad, CA), followed by purification and DNase-I digestion with RNeasy columns (Qiagen, Valencia, CA). We evaluated the quality of the RNA using an Agilent 2100 Bioanalyzer (Agilent Technologies). Total RNA was amplified using the Agilent Low RNA Input Fluorescent Linear Amplification Kit protocol. Starting with 500 ng of total RNA, cyanine (Cy)3- or Cy5-labeled cRNA was produced according to the manufacturer's protocol. For each two-color comparison, 750 ng each of Cy3- and Cy5-labeled cRNA was mixed and fragmented using the Agilent In Situ Hybridization Kit protocol (Agilent Technologies). We performed hybridizations on Agilent mouse 22K oligo assay for 17 hr in a rotating hybridization oven using the Agilent 60-mer oligo microarray processing protocol. Slides were washed as indicated in this protocol and then scanned with an Agilent Scanner. Data were obtained using the Agilent Feature Extraction software (version 7.5), employing defaults for all parameters. Two hybridizations with fluor reversals were performed for each RNA sample from each group.

Rosetta Resolver. Images and GEML (gene expression markup language) files, including error and p-values, were exported from the Agilent Feature Extraction software and deposited into the Rosetta Resolver system (version 4.0, build (Rosetta Biosoftware, Kirkland, WA). We combined the resultant ratio profiles. Intensity plots were generated for each ratio experiment, and genes were considered "signature genes" if the p-value was < 0.001.

Ingenuity Pathways Analysis. We further analyzed the signature genes with Ingenuity Pathways Analysis (Ingenuity Systems, Redwood City, CA; http://www.ingenuiry. com), a web-delivered application that enables biologists to discover, visualize, and explore relevant networks significant to their experimental results, such as gene expression array data sets. A data set containing gene identifiers and their corresponding expression values such as fold-changes and p-values was uploaded as a tab-delimited text file. Each gene identifier was mapped to its corresponding gene object in the Ingenuity Pathways Knowledge Base. A fold change cutoff of 1.5-fold and p < 0.001 was set to identify genes whose expression was differentially regulated. These genes, called "focus genes," were then used as the starting point for generating biological networks. To start building networks, the application queries the Ingenuity Pathways Knowledge Base for interactions between focus genes and all other gene objects stored in the knowledge base, then generates a set of networks with a network size of approximately 35 genes or proteins. Ingenuity Pathways Analysis then computes a score for each network according to the fit of the user's set of significant genes. The score is derived from a p-value and indicates the likelihood of the focus genes in a network being found together because of random chance. A score of 2 indicates a 1 in 100 change that the focus genes are together in a network because of random chance. Therefore, scores of 2 or higher have at least a 99% confidence level of not being generated by random chance alone. Biological functions are then calculated and assigned to each network.

Real-time RT-PCR analysis. We used real-time RT-PCR analysis to quantify the levels of expression of the selected genes (Liu et al. 2004). The forward and reverse primers for selected genes were designed using ABI Primer Express software (Applied Biosystems, Foster City, CA). Total RNA was reverse transcribed with MuLV reverse transcriptase and oligo-dT primers, then subjected to real-time PCR analysis using SYBR green PCR master mix (Applied Biosystems, Cheshire, UK). The relative differences in expression between groups were determined using cycle time (Ct) values as follows: The Ct values of the genes of interest were first normalized with [beta]-actin of the same sample; then the relative differences between control and treatment groups were calculated and expressed as relative increases, setting the control as 100%. Assuming the Ct value reflects the initial starting copy and there is 100% efficiency, a difference of one cycle is equivalent to a 2-fold difference in starting copy.

Western blot analysis. Tissues were homogenized (1:20, w:v) in PER-Tissue Protein Extraction buffer (Pierce, Rockford, IL) containing freshly added protease inhibitor cocktail (Calbiochem, La Jolla, CA) and 100 [micro]M phenylmethylsulfonyl fluoride. Cytosols were prepared by centrifugation at 15,000xg for 10 min at 4[degrees]C. Protein concentrations were determined using the dye-binding assay (Bio-Rad, Hercules, CA). Total protein (30 [micro]g) was subjected to electrophoresis on NuPAGE Bis-Tris gels (4-12%) (Invitrogen, San Diego, CA), followed by electrophoretic transfer to nitrocellulose membranes at 30 V for 1 hr. Membranes were blocked in 5% dried milk in TBST (15 mM Tris-HCl, pH 7.4, 150 mM NaCl, and 0.05% Tween 20) for 2 hr, followed by incubation with the primary antibody (1:200 to 1:1,000) in Blotto (Pierce, Rockford, IL) overnight at 4[degrees]C. After washes with TBST, the membranes were incubated in horse radish peroxidase-conjugated secondary antibody (1:4,000 to 1:10,000) for 1 hr and washed with TBST 3 times. Immunoblots were visualized using SuperSignal chemiluminescent substrate (Pierce, Rockford, IL).

Statistics. For microarray analysis, we cross-hybridized samples with Cy3 and Cy5. For Ingenuity Pathways Analysis, we used a Fisher's exact test to calculate a p-value to determine the probability that the biological function assigned to that network could be explained by chance alone. For real-time RT-PCR analysis, means and SEM of individual samples (n = 5-7) were calculated. For the comparisons of gene expression between two groups, Student's t-test was performed. For comparisons among three or more groups, data were analyzed using analysis of variance, followed by Duncan's multiple range test. The level of significance was set at p < 0.05 in all cases.


Microarray analysis of aberrantly expressed genes. The hepatocarcinogenic effects of inorganic arsenic have been verified in a study in which HCC developed in high incidence in male mice after in utero exposure (Waalkes et al. 2004b). Thus, total RNA was isolated from samples of control mouse liver, arsenic-exposed nontumorous normal liver, and arsenic-induced HCC taken at autopsy, and subjected to microarray analysis. Under the criteria of p < 0.001 by the Rosetta Resolver (version 4.0) system, the expression of 2,010 genes was significantly altered in arsenic-exposed normal liver samples compared with control, and 2,540 genes were altered in arsenic-induced HCC. The clustering analysis of these gene alterations clearly showed they generally occur in the same direction (increase or decrease) but are much more pronounced in arsenic-induced tumors than normal surrounding tissue from arsenic exposed mice (Table 1, Figure 1). Examples of a cluster showing increased genes (shown in red) and an example of a gene cluster showing decreased genes (green) are shown in Figure 1. Generally, gene alterations seen in the present study are largely consistent with the previous, more limited gene analysis (Liu et al. 2004) of our first transplacental arsenic carcinogenesis study (Waalkes et al. 2003). The significant gene expression alterations (p < 0.001 and 1.5-fold cutoff) were further selected for Ingenuity Pathway Analysis.


Ingenuity Pathways Analysis. To further analyze the biological significance of these alterations in gene expression, we used the Ingenuity Pathways Analysis; an example of the highest score in the analysis from arsenic-induced tumors (Figure 2) is depicted. The intensity of the node color indicates the degree of increased (red) or decreased (green) expression in arsenic-induced HCC. Biological functions were assigned to each gene network by using the findings extracted from the published scientific literature and stored in the Ingenuity Pathways Knowledge Base ( products/PathwaysKnowledge.pdf) and are ranked according to the significance of that biological function to the network. The activation of c-myc oncogene and its central role in related pathway alterations are consistent with the published literature on arsenic (Chen et al. 2001b), and could be a major component of its hepatocarcinogenic potential.


Real-time RT-PCR analysis of aberrantly expressed genes. To confirm and extend microarray results, we performed real-time RTPCR analysis of selected genes using individual samples from control mouse liver, arsenic-exposed nontumorous livers, and arsenic-induced HCC. Generally, real-time RT-PCR confirmed microarray results with > 90% concordance but tended to show more pronounced changes than microarray analysis (Table 1). For HCC biomarkers, alpha-fetoprotein (AFP, 19-fold), plasminogen activator inhibitor-1 (PAI-1, 9-fold), cytokeratin 8 (6-fold), cytokeratin 18 (3-fold) and cytokeratin 19 (11-fold), were dramatically increased in arsenic-induced HCC. The oncogenes c-myc, c-met, k-ras and the neoplastic progression protein-3 (Npn3) were also increased 2- to 3-fold in arsenic-induced HCC and nontumorous, normal liver from arsenic exposed mice, while the tumor suppressors BRCA1 and BRCA2 decreased 30-50%.

The positive cell cycle regulators cyclin D1 (5-fold), cyclin E (5-fold), cdk2na (14-fold), cdk2nb (6-fold), cdk4 (4-fold), and PCNA (3-fold) were increased as a result of arsenic exposure, while the cell cycle negative regulator p16 decreased 40%. The expression of insulin-like growth factor-1 (IGF-1, 60% of control) was decreased, while the expression of IGF-2 was increased 4-fold. The IGF-binding proteins (IGFBP1, 9-fold), IGFBP3 (3-fold), and IGFBP5 (2.4-fold) were all increased to some extent.

Arsenic produces oxidative stress within cells as a possible mechanism of its toxicity (Liu et al. 2001a). Stress-related genes, including various glutathione S-transferases (GST-alpha, GST-mu, GST-pi, and GST-theta) and early growth response protein 1 (EGR1), increased 2.5- to 4.5-fold. In addition, Cu,Zn-superoxide dismutase (SOD1) and ceruloplasmin (Cu-binding protein) were also increased approximately 3-fold by arsenic. In comparison, no major changes occurred in the expression of heme oxygenase-1 (HO-1), a biomarker for arsenic-induced oxidative stress (NRC 1999), and the expression of metallothionein-1 (MT-1) actually decreased 50%.

A feminized pattern of metabolic enzymes has been noted in male livers of mice bearing arsenic-induced HCC after in utero exposure (Waalkes et al. 2004a). Marked elevation in expression of the female predominant cytochtome P450 (CYP)2A4 (25-fold), and significant increases (2- to 3-fold) of female dominant CYP2B9 (2.6-fold) and CYP2D9 were evident. In contrast, expression of the male dominant CYP7B1, CYP2F2, and CYP41 were all decreased by approximately 50% by arsenic exposure. Further evidence for feminization includes increased expression of aldo-keto reducrase lc18 (Akrlc18) and hydroxysteroid 17[beta] dehydrogenase 7 (HSD 17[beta]7), as well as ER-[alpha] linked overexpression of trefoil factor 3 (TFF3) and cysteine-rich protein 61 (Cyr61). No apparent changes occurred for CYP2C39, CYP2E1, CYP2J5, CYP3A25, and CYP4A14 (data not shown). Interestingly, the enzymes for lipid metabolism such as lipoprotein lipase (Lpl, 33-fold), cytosolic acyl-CoA thioesterase (Ctel, 5-fold), and proteasome 26S subunit ATPase-3 (Pmsc3, 4-fold) were increased. Conversely, betaine homocysteine methyltransferase (BHMT, 60% of control), serum amyloid 3 (Saa3, 30% of control), and sulfotransferase-related protein 2 (SULT-X2, 1% of control) were decreased.

For cell--cell interaction genes and genes involved in signal transduction, marked increases occurred in annexin A2 (48-fold), nidogen 1 (50-fold), E-cadherin (11-fold), and [beta]-catenin (7-fold) in arsenic-induced HCC. Moderate increases in the ras homolog gene family U (Rhou, 4-fold), in fibronection (CTGF, 4-fold), and in prostaglandin-endoperoxide synthase 2 (Ptgs-2, 5.5-fold) were also evident. In contrast, the prolactin receptor (Prlr, 40% of control) and the epidermal growth factor receptor (Egfr, 40% of control) were decreased as a result of in utero exposure to inorganic arsenic.

Western blot analysis of aberrantly expressed proteins. We also performed Western blot analysis on selected gene products (Figure 3). Western blot analysis largely confirmed the gene expression results and clearly showed the increases in the expression of potential oncogenes AFP, K-ras, and c-Myc in both arsenic-exposed nontumorous livers and arsenic-induced HCC. The cell cycle regulators, such as ER-[alpha], the ER-[alpha] linked cyclin D1, cyclin-dependent kinase 4 (cdk4), and proliferating cell nuclear antigen (PCNA), all followed this pattern of high in tumor tissues, intermediate in tumor-surrounding livers and low in control liver. The HCC biomarkers cytokeratin 8 and plasminogen activator inhibitor 1 (PAI-1) were all significantly increased in arsenic-induced HCC, and also higher in arsenic-exposed tumor-surrounding tissues. Endothelial growth factor receptor (EGFR) was down-regulated in arsenic-induced HCC. The expression of [beta]-actin was consistent among lanes.



Our most recent transplacental arsenic carcino-genesis study (Waalkes et al. 2004b) confirmed the hepatocarcinogenic potential of arsenic in adult male mice after transplacental exposure (Waalkes et al. 2003), and it also provided an opportunity for a genomewide gene expression analysis. The 22K mouse chip array revealed several novel pathways and gene expression alterations associated with arsenic-induced HCC and in arsenic-exposed nontumorous normal liver samples, which were not detected in previous limited gene expression analysis. Liver is a major target organ for arsenic in rodents and in humans (Liu et al. 2000; 2002; Santra et al. 2000). In other studies, HCC formation has been associated with arsenic exposure in humans (Centeno et al. 2002; Chen et al. 1997; Chin et al. 2004; Zhou et al. 2002). Therefore, the present gene profiling study in mice of a concordant human target tissue is noteworthy because it clearly demonstrates that multiple genetic events occurred during the carcinogenic process in the liver induced by in utero exposure to arsenic. It is reasonable to anticipate a complicated series of genetic interactions in arsenic-induced carcino-genesis, which this study certainly shows. However, the present results also provide a variety of candidate genes to investigate in greater detail, such as with time-course experiments, to define events early after transplacental arsenic exposure. Furthermore, recent evidence indicates that early life chemical exposures may aberrantly "reprogram" gene expression patterns, thus resulting in altered growth responses and cancer later in life, as with diethylstilbestrol and uterine cancer (Cook et al. 2005). Consistent with this concept, the altered gene expression patterns seen in adults after in utero arsenic exposure could have resulted from the early life reprogramming during a critical stage in development.

Clustering analysis clearly shows that the gene changes in HCC and normal liver samples taken from mice exposed to arsenic in utero are for the most part directionally consistent but with quantitatively greater changes in the arsenic-induced tumors. The gene expression alterations associated with arsenic hepato-carcinogenesis have an important impact on as many as 50 biological networks shown by Ingenuity Pathways Analysis to be significantly altered or interrupted. The observation that a large number of graded gene expression changes occurred both in nontumorous and in tumorous liver samples from adults exposed to arsenic in utero is important because it implies that complex changes initiated during gestation appear to have persisted into adulthood. Some of those alterations are very likely relevant to the carcinogenic process. The complex nature of this arsenic-induced response argues against mutational activation of a few key pathways and perhaps points toward other mechanisms for persistent gene expression change. For example, the central network role for c-Myc seen in the present study is consistent with c-myc activation in arsenic-transformed rat liver cells (Chen et al. 2001b), in hamster embryo cells (Takahashi et al. 2002), and in murine fibroblasts (Trouba et al. 2000). This central network role also agrees with that suggested by results from arsenic-induced skin tumors (Germolec et al. 1998) and from HCC induced by in utero arsenic exposure (Liu et al. 2004). Overexpression of c-myc may be caused by arsenic-induced DNA hypomethylation of the c-myc promoter region (Takahashi et al. 2002). The activation of c-myc oncogene can in turn result in many other gene expression changes. For example, the increased expression of the N-myc downstream regulated gene 1 (NDRG1) is associated with HCC formation. The increased expression of stearoyl-CoA desaturase-1 (SCD-1) plays a key role in lipogenic gene expression and in metabolic syndrome, which coincides with marked elevations of lipoprotein lipase (Lpl, 33-fold) and cytosolic acyl-CoA thioesterase-1 (Ctel, 5-fold) in arsenic-induced HCC. This increased expression could also be important for arsenic-induced hepatic steatosis (Chen et al. 2004). Interestingly, in this network, the increase in C-myc is associated with a decrease in metallothionein-1 expression (MT-1), which was confirmed by RT-PCR analysis. MT is an adaptive protein in response to arsenic exposure (Liu et al. 2000). The decrease in MT could be a marker for liver tumor progression because MT is poorly expressed in both mouse and human HCC (Waalkes et al. 1996). Determining the changes that are specific to arsenic and the changes that are part of the potentially autonomous process of liver oncogenesis will be a major challenge, but the present work opens various avenues for further study.

In addition to c-myc overexpression, the activation of various oncogenes such as k-ras and c-met was also evident following transplacental arsenic exposure, as seen with arsenic-transformed rat liver cells (Chen et al. 2001a). Overexpression of k-ras is also associated with arsenic-induced malignant transformation in human prostate epithelial cells (Benbrahim-Tallaa et al. 2005). Ha-ras mutation and overexpression, as in genetically altered Tg.AC mice, is associated with arsenic-induced co-promotion of skin tumors (Germolec et al. 1998). In a fashion similar to c-myc, DNA hypomethylation could be responsible for ras oncogene overexpression, and chronic arsenic exposure in vivo appears to induce a loss of methylation at several cytosine sites within the promoter region of the hepatic Ha-ras gene in mice (Okoji et al. 2002). The Ras-mediated signal transduction molecule Rhou (ras homolog gene family U) was also increased 3- to 4-fold in arsenic-exposed tissues in the present study. The HCC biomarkers [alpha]-fetoprotein, plasminogen activator inhibitor 1 (PAI-1), cytokeratin 8, cytokeratin 18, and cytokeratin 19, as well as the neoplastic progression protein-3, were all significantly increased, consistent with HCC pathobiology and previous findings with arsenic (Liu et al. 2004). Conversely, the tumor suppressor genes BRCA1 and BRCA2 were decreased. BRCA1 protein interacts directly with ER-[alpha], thereby resulting in inhibition of estradiol-stimulated ER-[alpha] transcriptional activity (Ma et al. 2005). Thus, down-regulation of BRCA1 and BRCA2 could play a role in the overexpression of ER-[alpha] and ER-[alpha]-linked gene expression observed in this model of arsenic carcinogenesis (Waalkes et al. 2004a).

The tumors (in the liver, ovary, adrenal, lung) and proliferative lesions (in the uterus and oviduct) induced by in utero arsenic exposure can all similarly be induced by estrogenic carcinogens (Waalkes et al. 2003; 2004b). Indeed, prior results demonstrated the over-expression of ER-[alpha] with a nuclear localization (active form) in adult male liver after in utero arsenic exposure (Waalkes et al. 2004a; Chen et al. 2004), a result confirmed by Western blot analysis in the present study. This finding leads to the hypothesis that arsenic could somehow produce estrogenic-like effects, possibly directly or indirectly through stimulation of ER-[alpha], thus resulting in tumor formation (Waalkes et al. 2004a). Overexpression of ER-[alpha] could be caused by arsenic-induced DNA hypomethylation of the promoter region of the ER-[alpha] gene (Chen et al. 2004; Waalkes et al., 2004a). Such overexpression is associated with the feminization pattern of liver metabolic enzymes in male liver bearing arsenic-induced HCC (Liu et al. 2004; Waalkes et al. 2004a). In the present study, marked elevation of the female predominant CYP2A4, CYP2B9, and CYP2D9 and significant decreases in male dominant CYP7B1, CYP2F2, and CYP41 were evident following transplacental arsenic exposure in male offspring, consistent with this hypothesis. The contribution of ER-[alpha] signaling pathways to arsenic-induced HCC could be multifactorial, including the increased trefoil factor-3 (TFF3), cychn D1, and the CCN family members cysteine-rich 61 (Cyr61) and connective tissue growth factor (CTGF). Overexpression of TFF3 is proposed to be a critical process in hepatocarcinogenesis (Okada et al. 2005), and overexpression of Cyr61 and CTGF is associated with recurrence and metastasis of HCC (Zeng et al. 2004).

Estrogen-induced progression through the [G.sub.1] phase of the cell cycle is preceded by increased expression of the [G.sub.1]-phase regulatory proteins c-Myc and Cyclin D1 (Prall et al. 1998). Cyclin D1 overexpression is important for HCC formation and is considered a hepatic oncogene (Deane et al. 2001). Overexpression of cyclin D1 has been reported in arsenic-transformed cells (Chen et al. 2001b), during arsenic-induced skin co-carcinogenicity in mice (Rossman et al. 2001), in dimethylarsinic acid--induced bladder proliferative lesions in rats (Wei et al. 2002), in chronic arsenate-exposed rats (Cui et al. 2004), and in the livers of mice bearing HCC induced by in utero exposure to arsenic (Liu et al. 2004). Cyclin D1 overexpression, together with other positive cell cycle regulators such as cyclin E, cdk4, cdkn2a, cdkn2b, and PCNA was evident in arsenic-exposed tissues in the present study. Thus, cell cycle dysregulation, as manifested in cyclin D1 overexpression, appears to be a consistent event in arsenic-induced oncogenesis. In comparison, expression of the negative cell cycle regulator p16 was decreased, consistent with prior observations with arsenic (Chen et al. 2001a; Liu et al. 2004). In addition to these cell cycle regulators, annexin A2 was also dramatically increased (48-fold) in arsenic-induced HCC. Annexins belong to a family of the calcium-dependent phospholipid binding proteins and are substrates of receptor tyrosine kinases. Annexin A2 overexpression is common in various carcinomas (Emoto et al. 2001), and annexin A2 can interact with c-Myc in increasing cell proliferation (Micldeburgh et al. 2005). Dysregulation of the IGF axis, including IGF-1 and IGF-2, and IGF binding proteins, was evident in our prior work (Liu et al. 2004) and in our present studies. A decrease in IGF-1 and an increase in IGFBP1 in arsenic-exposed livers are similar to findings with the nongenotoxic model carcinogens such as oxazepam and Wyeth-14,643 (Iida et al. 2003). Dysregulation of the IGF axis may also well contribute to uncontrolled cell proliferation and hepato-carcinogenesis (Scharfand Braulke 2003).

The expression of oxidative stress-related genes is associated with arsenic toxicity and cell proliferation (Liu et al. 2001; Pi et al. 2003). For example, overexpression of early growth protein 1 (EGR1) is associated with arsenic-induced proliferation in urinary bladder cells (Simeonova et al. 2000) and in arsenic-induced HCC (Liu et al. 2004). The activation of transcription factor Nrf2 by arsenic and the Nrf2-mediated overexpression of antioxidants such as Cu,Zn superoxide dismutase (SODI) is evident in arsenic-exposed cells (Pi et al. 2003). Expression of SOD1 and the Cu-binding protein ceruloplasmin was increased in arsenic-exposed liver and in arsenic-induced liver tumors in the present work. The increases in these acute phase proteins may have clinical relevance because increased ceruloplasmin (Bencko et al. 1988) and SOD1 (Lu et al. 2001) have been reported in arsenic-exposed humans. Heine oxygenase-1, a biomarker for acute arsenic-induced oxidative stress (Liu et al. 2001a; NRC 1999), was not significantly altered in the present study. In comparison, GST-alpha, GST-mu, GST-pi, and GST-theta expressions were all increased following in utero arsenic exposure, similar to previous observations in chronic arsenic exposure settings (Liu et al. 2000; Lu et al. 2001; Xie et al. 2004). Increased GSTs likely play a role in conjugation and detoxication of lipid peroxides produced by arsenic, but they also play a role for cellular efflux of arsenic via MRP pumps (Leslie et al. 2004; Liu et el. 2001b). The increased demand for GSH utilization may activate the use of homocysteine for GSH synthesis, rather than for S-adenosylmethionine (SAM), and, consequently, disrupt cellular methyl homeostasis (Lu et al. 2002). In this regard, expression of betaine-homocysteine methyltransferase was markedly decreased, and it is a key enzyme in SAM recycling. This disruption of SAM production may contribute to a cellular environment conducive to errors in DNA methylation, which can be a contributing factor to aberrant gene expression.

Both [beta]-catenin and E-cadherins are important cell--cell communication molecules. The overexpression of [beta]-catenin is linked to cyclin D1 overexpression in HCC (Iida et al., 2003). Furthermore, [beta]-catenin can also affect tumor progression by stimulating proliferation, and overexpression is associated with a poor prognosis for patients with HCC. E-cadherin is a cell--cell adhesion molecule that plays a key role in the development and maintenance of cell polarity. Dysregulation of E-cadherin is also associated with HCC (Calvisi et al. 2004). Nidogen-1 acts as a bridge between the extra-cellular matrix molecules laminin-1 and collagen IV, and it participates in the assembly of the basement membranes. In the present study, nidogen 1 (50-fold), [beta]-catenin (7-fold), and E-cadherin (11-fold) were all dramatically increased in transplacental arsenic-induced HCC and in arsenic-exposed liver tissues. Conversely, the prolactin receptor and EGFR were decreased in arsenic-induced HCC, thereby suggesting that the dysregulation of cell-cell communications and signal transduction pathways could be another important aspect of arsenic hepatocarcinogenesis, as has been proposed for liver cancer in general.

In summary, we used a genomewide analysis to dissect further the toxicogenomics changes of transplacental arsenic hepatocarcinogenesis in the mouse. These findings clearly demonstrate that arsenic carcinogenesis in the liver involves a complex interplay between multiple genetic events, including stimulation of oncogene expression, liver feminization, cell cycle dysregulation, and disruption of cell--cell communication. This study indicates that early life exposure to arsenic during a critical stage in development may have resulted in aberrant genetic reprogramming that leads to events associated with hepatocarcinogenesis later in life. Finally, the present results highlight the importance of protecting pregnant women from excessive arsenic exposure.

Received 22 July 2005; accepted 6 October 2005.


Anderson LM, Diwan BA, Fear NT, Roman E. 2000. Critical windows of exposure for children's health: cancer in human epidemiological studies and neoplasms in experimental animal models. Environ Health Perspect 108(suppl 3):573-594.

Benbrahim-Tallaa L, Waterland RA, Styblo M, Anhanzar WE, Webber MM, Waalkas MP. 2005. Molecular events associated with arsenic-induced malignant transformation of human prostate epithelial cells: aberrant genomic DNA methylation and K-ras oncegene activation. Toxicol Appl Pharmacol 206:288-298.

Bencko V, Wagner V, Wagnerova M, Batora J. 1988. Immunological profiles in workers of a power plant burning coal rich in arsenic content. J Hyg Epidemiol Microbiol Immunol. 32:137-146.

Calvisi Dr, Ladu S, Conner EA, Factor VM, Thorgeirsson SS. 2004. Disregulatien of E-cadherin in transgenic mouse models of liver cancer. Lab Invest 84:1137-1147.

Centeno JA, Mullick FG, Martinez L, Page NP, Gibb H, Longfellow D, et el. 2C02, Pathology related to chronic arsenic exposure. Environ Health Perspect 110(suppl 5):883-886.

Chattopadhyay S, Bhaumik S, Nag Chaudhury A, Des Gupta S, 2002. Arsenic-induced changes in growth development and apoptosis in neonatal and adult brain cells in viva and in tissue culture. Toxicol Lett 128:73-84.

Chen C J, Yu MW, Liaw, YE. 1997. Epidemiological characteristics and risk factors of hepatocellular carcinoma. J Gastroenterol Hepatol 12:S294-308.

Chen H, Li S, Liu J, Diwan BA, Barrett JC, Waalkes MP. 2004. Chronic inorganic arsenic exposure induces hepatic global and individual gene hypomethylation: implications for arsenic hepatocarcinogenesis. Carcinogenesis 25:1779-1786.

Chen H, Liu J, Merrick BA, Waalkes MP. 2001a. Genetic events associated with arsenic-induced malignant transformation: applications of cDNA microarray technology. Mol Carcinog 30:79-87.

Chen H, Liu J, Zhao CQ, Diwan BA, Merrick BA, Waalkes MP. 2001b. Association of c-myc overexpression and hyperproliferation with arsenite-induced malignant transformation. Toxicol Appl Pharmacol 175:260-268.

Chen Y, Ahsan H. 2004. Cancer burden from arsenic in drinking water in Bangladesh. Am J Public Health 94:741-744.

Chiu HE. He SC, Wang LY, Wu TN, Yang CY. 2004. Does arsenic exposure increase the risk for liver cancer? J Toxicol Environ Health A 67:1491-1500.

Concha G, Vogler G, Lezcano D, Nermell B, Vahter M. 1998. Exposure to inorganic arsenic metabolites during early human development. Toxicol Sci 44:185-190.

Cook JD, Davis BJ, Cai SL, Barrett JC, Conti C J, Walker CL 2005. Interaction between genetic susceptibility and early life environmental exposure determines tumor suppressor gone penetrance. Proc Natl Acad Sci USA 102:8644-8649.

Cui X, Li S, Shreim A, Kobayashi Y, Hayakawa T, Kanno S, et al. 2004. Subchronic exposure to arsenic through drinking water alters expression of cancer-related genes in rat liver. Toxicol Pathol 32:64-72.

Deane NG, Parker MA, Aramandla R, Diehl L, Lee WJ, Washington MK, et al. 2001. Hepatocellular carcinoma results from chronic cyclin D1 overexpression in transgenic mice. Cancer Res 61:5389-5395.

Emote K, Sawada H, Yamada Y, Fujimoto H, Takahama Y, Ueno M, et al. 2001. Annexin II overexpressien is correlated with poor prognosis in human gastric carcinoma. Anticancer Res 21:1339-1345.

Germolec DR, Spalding J, Yu HS, Chen GS, Simeonova PP, Humble MC, et al. 1998. Arsenic enhancement of skin neoplasia by chronic stimulation of growth factors. Am J Pathol 153:1775-1785.

IARC (International Agency for Research on Cancer). 1987. Overall Evaluations of Carcinogenicity: An Updating of IARC Monographs Volumes 1 to 42. IARC Monogr Eval Carcinog Risks Hum (suppl 7).

Iida M, Anna CH, Harris J, Bruno M, Wetmore B, Dubin JR, et al. 2003. Changes in global gene end protein expression during early mouse liver carcinogenesis induced by non-genotoxic model carcinogens oxazepam and Wyeth-14,643. Carcinogenesis 24:757-770.

Institute of Laboratory Animal Resources. 1996. Guide for the Care and Use of Laboratory Animals. 7th ed. Washington, DC:The National Academies Press.

Kitchin KT. 2001. Recent advances in arsenic carcinogenesis: modes of action, animal model systems, and methylated arsenic metabolites. Texicol Appl Pharmacol 172:249-261.

Leslie EM, Haimeur A, Waalkes MP. 2004. Arsenic transport by the human multidrug resistance protein 1 (MRP1/ABCC1). Evidence that a tri-glutathione conjugate is required. J Biol Chem 279:32700-32708.

Liu J, Chen H, Miller DS, Saavedre JE, Keefer LK, Johnson DR, et al. 2001a. Overexpression of glutathione S-transferase II and multidrug resistance transport proteins is associated with acquired tolerance to inorganic arsenic. Mel Pharmacol 60:302-309.

Liu J, Kadiiska MR, Liu Y, Lu T, Qu W, Waalkes MP 2001b. Stress-related gone expression in mice treated with inorganic arsenicals. Toxicol Sci 61:314-320.

Liu J, Liu Y, Goyer RA, Achanzar W, Waalkes MP. 2000. Metallethionein-I/II null mice are more sensitive than wild-type mice to the hepatotoxic and nephrotoxic effects of chronic oral or injected inorganic arsenicals. Toxicol Sci 55:460-467.

Liu J, Xie Y, Ward JM, Diwan BA, Waalkes MP. 2004. Toxicogenomic analysis of aberrant gene expression in liver tumors and nontumorous livers of adult mice exposed in utero to inorganic arsenic. Toxicol Sci 77:249-257.

Liu J, Zheng B, Aposhian HV, Zhou Y, Chen ML, Zhang A, et al. 2002. Chronic arsenic poisoning from burning high-arsenic-containing coal in Guizhou, China. Environ Health Perspect 110:119-122.

Lu SC, Tsukamoto H, Mate JM. 2002. Role of abnormal methionine metabolism in alcoholic liver injury. Alcohol 27:155-162.

Lu T, Liu J, LeCluyse EL, Zhou YS, Chang ML, Waalkes MP. 2001. Application of cDNA microarray to the study of arsenic-induced liver diseases in the population of Guizhou, China. Toxicol Sci 59:185-192.

Ma YX, Tomita Y, Fan S, Wu K, Tong Y, Zhao Z, et al. 2005. Structural determinants of the BRCA1 and estrogen receptor interaction. Oncogene 24:1831-1846.

Mickleburgh I, Burtle B, Hellas H, Campbell G, Chrzanowska-Lightowlers Z, Vedeler A, et al. 2005. Annexin A2 hinds to the localization signal in the 3' untranslated region of c-myc mRNA. FEBS J 272:413-21.

Morales KH, Ryan L, Kuo T-L, Wu M-M, Chen C-J. 2000. Risk of internal cancers from arsenic in the drinking water. Environ Health Perspect 108:655-661.

NRC (National Research Council). 1999. Arsenic in the Drinking Water. Washington, DC:National Academy Press.

Okada H, Kimura MT, Tan G, Fujiwara K, Igarashi J, Makuuchi M, et al. 2005. Frequent trefoil factor 3 (TFF3) everexpression end promoter hypomethylation in mouse and human hepatocellular carcinomas. Int J Oncol 26:369-377.

Okoji RS, Yu RC, Maronpot RR, Froines JR. 2002. Sodium arsenite administration via drinking water increases genome-wide and Ha-ras DNA hypomethyletion in methyl-deficient C57BL/6J mine. Carcinogenesis 23:777-785.

Pi J, Qu W, Reece JM, Kumagai Y, Waalkes MP. 2003. Transcription factor Nrf2 activation by inorganic arsenic in cultured keratinocytes: involvement of hydrogen peroxide. Exp Cell Hes 290:234-245.

Prall OW, Rogan EM, Musgrove EA, Watts CK, Sutherland RL. 1998. c-Myc or cyclin 131 mimics estrogen effects on cyclin E-Cdk2 activation and cell cycle reentry. Mol Cell Biol 18:4499-4508.

Rossman TG, Uddin AN, Burns FJ, Bosland MC. 2001. Arsenite is a cocarcinogen with solar ultraviolet radiation for mouse skin: an animal model for arsenic carcinogenesis. Toxicol Appl Pharmacol 176:64-71.

Santra A, Maiti A, Das S, Lahiri S, Charkaborty SK, Mazumder DN. 2000. Hepatic damage caused by chronic arsenic toxicity in experimental animals. J Toxicol Clin Toxicol 38:395-405.

Scharf JG, Braulke T. 2003. The role of the IGF axis in hepato-carcinogenesis. Herin Metab Res 35:685-693.

Simeonova PP, Wang S, Toriuma W, Kommineni V, Matheson J, Unimye N, et al. 2000. Arsenic mediates cell proliferation and gone expression in the bladder epithelium: association with activating protein-1 transactivation. Cancer Res 60:3445-3453.

Takahashi M, Barrett JC, Tsutsui T. 2002. Transformation by inorganic arsenic compounds of normal Syrian hamster embryo cells into a neoplastic state in which they become anchorage-independent and cause tumors in newborn hamsters. Int J Cancer 99:629-634.

Trouba KJ, Weuson EM, Vorce RL. 2000. Sodium arsenite-induced dysregulation of proteins involved in proliferative signaling. Toxicol Appl Pharmacol 164:161-170.

Waalkes MP, Diwan BA, Rehm S, Ward JM, Moussa M, Cherian MG, et al. 1996. Down-regulation of metallothionein expression in human and murine hepatocellular tumors: association with the tumor-necrotizing and antineoplastic effects of cadmium in mice. J Pharmacol Exp Ther 277:1026-1033.

Waalkes MP, Liu J, Chen H, Xie Y, Achanzar WE, Zhou YS, et al. 2004a. Estrogen signaling in livers of male mice with hepatocellular carcinoma induced by exposure to arsenic in utero. J Natl Cancer Inst 96:466-474.

Waalkes MP, Ward JM, Diwan BA 2004b. Induction of tumors of the liver, lung, ovary, and adrenal in adult mice after brief maternal gestational exposure to inorganic arsenic: promotional effects of postnatal phorbol ester exposure on hepatic and pulmonary, but not dermal cancers. Carcinogenesis 25:133--141.

Waalkes MP, Ward JM, Liu J, Diwan BA. 2003. Transplacental carcinogenicity of inorganic arsenic in the drinking water: induction of hepatic, ovarian, pulmonary, and adrenal tumors in mice. Toxicol Appl Pharmacol 186:7-17.

Wei M, Wanibuchi H, Morirnura K, Iwai S, Yoshida K, Endo G, et el. 2002. Carcinogenicity of dimethylarsinic acid in male F344 rats and genetic alterations in induced urinary bladder tumors. Carcinogenesis 23:1387-1397.

Xie Y, Trouba KJ, Liu J, Waalkes MP, Germolec OR. 2004. Biokinetics and subchronic toxic effects of oral arsenite, arsenate, monomethylarsonic acid, and dimethylarsinic acid in v-Ha-ras transgenic (Tg.AC) mice. Environ Health Perspect 112-:1256-1263.

Zeng ZJ, Yang LY, Ding X, Wang W. 2004. Expressions of cysteine-rich61, connective tissue growth factor, and Nov genes in hepatocellular carcinoma and their clinical significance. World J Gastroenterol 10:3414-3418.

Zhou YS, Du H, Cheng M-L, Liu J, Zhang XJ, Xu L 2002. The investigation of death from diseases caused by coal-burning type of arsenic poisoning. Chin J Endemiol 21:484-486.

Jie Liu, (1) Yaxiong Xie, (1) Danica M.K. Ducharme, (2) Jun Shen, (1) Bhalchandra A. Diwan, (3) B. Alex Merrick, (2) Sherry F. Grissom, (2) Charles J. Tucker, (2) Richard S. Paules, (2) Raymond Tennant, (2) and Michael P. Waalkes (1)

(1) Inorganic Carcinogenesis Section, Laboratory of Comparative Carcinogenesis, National Cancer Institute at the National Institute of Environmental Health Sciences, and (2) National Center For Toxicogenomics, National Institute of Environmental Health Sciences, National Institutes of Health, Department of Health and Human Services, Research Triangle Park, North Carolina, USA; (3) Basic Research Program, Science Applications International Corporation, National Cancer Institute, National Institutes of Health, Department of Health and Human Services, Frederick, Maryland, USA

Address correspondence to M.P. Waalkes, Inorganic Carcinogenesis Section, NCI at NIEHS, Mail Drop F0-09, Research Triangle Park, NC 27709 USA. Telephone: (919) 541-2328. Fax: (919) 541-3970. E-mail: waalkes@

The authors thank W. Qu, J-F. Coppin, and L. Keefer for their critical review of this manuscript.

The content of this publication does not necessarily reflect the views or policies of the Department of Health and Human Services.

Research was supported in part by the Intramural Research Program of the NIH, National Cancer Institute, Center for Cancer Research, the National Center for Toxicogenomics, and the National Cancer Institute under contract NO1-CO-12400.

The authors declare they have no competing financial interests.
Table 1. Real-time RT-PCR and microarray analysis of liver samples
from adult male C3H mice exposed to arsenic in utero.

 Accession Control
Gene categories (a) no. (a) (PCR)

Oncogenes and HCC-related
 alpha-fetoprotein V00743 1.0 [+ or -] 0.2
 c-myc X01023 1.0 [+ or -] 0.2
 c-met Y00671 1.0 [+ or -] 0.2
 K-ras U49448 1.0 [+ or -] 0.2
 PAI-1, plasminogen M33960 1.0 [+ or -] 0.3
 activator inhibitor-1
 Cytokeratin-8 X12789 1.0 [+ or -] 0.2
 Cytokeratin-18 Ml_1686 1.0 [+ or -] 0.3
 Cytokeratin-19 NM_008471 1.0 [+ or -] 0.4
 BRCA1 U31625 1.0 [+ or -] 0.3
 BRCA2 U65594 1.0 [+ or -] 0.1
 Npn3, neoplastic Z31362 1.0 [+ or -] 0.4
 progression protein-3

Cell cycle regulators
 and IGFs
 Cychn D1 M64403 1.0 [+ or -] 0.2
 Cyclin E X75888 1.0 [+ or -] 0.1
 Cdk2na NM_009877 1.0 [+ or -] 0.2
 Cdk2nb AF_059567 1.0 [+ or -] 0.3
 Cdk4 L01640 1.0 [+ or -] 0.3
 PCNA X53068 1.0 [+ or -] 0.1
 P16 U79632 1.0 [+ or -] 0.3
 IGF-1 X04480 1.0 [+ or -] 0.1
 IGF-2 M14951 1,0 [+ or -] 0.2
 IGFBP1 X81579 1.0 [+ or -] 0.3
 IGFBP3 X81581 1.0 [+ or -] 0.4
 IGFBP5 X81583 1.0 [+ or -] 0.2

Stress-related genes
 GST-alpha4 AK008490 1.0 [+ or -] 0.4
 GST-mu J03953 1.0 [+ or -] 0.4
 GST-theta X98055 1.0 [+ or -] 0.5
 GST-pi NM_013541 1.0 [+ or -] 0.4
 EGR1,early response M20157 1.0 [+ or -] 0.5
 SOD-1 M01143 1.0 [+ or -] 0.4
 Ceruloplasmin U49430 1.0 [+ or -] 0.1
 HO-1, heme oxygenase-1 M33203 1.0 [+ or -] 0.1
 MT-1 BC027262 1.0 [+ or -] 0.2

Genes for metabolic
 CYP2A4 J03549 1.0 [+ or -] 0.1
 CYP2F2 M77497 1.0 [+ or -] 0.2
 CYP2B9 M21855 1.0 [+ or -] 0.4
 CYP2D9 M27168 1.0 [+ or -] 0.4
 CYP3A41 NM_017396 1.0 [+ or -] 0.5
 CYP7B1 U36993 1.0 [+ or -] 0.3
 Akr1c18, aldo-keto NM_134066 1.0 [+ or -] 0.5
 reductase 1cl8
 HSD1707 NM_010476 1.0 [+ or -] 1.4
 TFF3, trefoil factor 3 NM_011575 1.0 [+ or -] 0.1
 Cyr61, cysteine-rich NM_010516 1.0 [+ or -] 1.0
 protein 61
 Lp1, lipoprotein lipase NM_008509 1.0 [+ or -] 0.1
 Cte1, cytosolic acyl-CoA NM_012006 1.0 [+ or -] 0.2
 Pmsc3 proteasome 26S D49686 1.0 [+ or -] 1.1
 subunit, ATPase3
 BHMT, homocysteine AF033381 1.0 [+ or -] 0.1
 Saa3, serum amyloid 3 NM_011315 1.0 [+ or -] 0.3
 SULT-X2 AF26075 1.0 [+ or -] 0.1

Cell communication and
 signal transduction
 Annexin A2 M14044 1.0 [+ or -] 0.3
 Nid1, nidogen 1 NM_010917 1 0 [+ or -] 0.2
 [beta]-catenin NM_007614 1.0 [+ or -] 0.3
 E-cadherin NM_009864 1.0 [+ or -] 0.3
 Ptgs-2, prostaglandin- NM_011198 1.0 [+ or -] 0.4
 endoperoxidesynthase 2
 Rhou, ras homolog gene NM_133955 1.0 [+ or -] 0.2
 family U
 CTGF, fibronectin NM_022266 1.0 [+ or -] 0.3
 Prlr, prolactin receptor NM_11169 1.0 [+ or -] 0.4
 Eafr, enidermal orowth NM_07912 1.0 [+ or -] 0.2
 factor receptor

Gene categories (a) PCR Array-fold

Oncogenes and HCC-related
 alpha-fetoprotein 2.3 [+ or -] 0.5 NA
 c-myc 2.2 [+ or -] 0.5 1.67 *
 c-met 2.4 [+ or -] 0.6 1.03
 K-ras 1.4 [+ or -] 0.4 1.41
 PAI-1, plasminogen 2.7 [+ or -] 0.9 NA
 activator inhibitor-1
 Cytokeratin-8 1.6 [+ or -] 0.2 NA
 Cytokeratin-18 1.3 [+ or -] 0.3 1.04
 Cytokeratin-19 12.1 [+ or -] 4.7 * 1.53 *
 BRCA1 0.7 [+ or -] 0.1 1.08
 BRCA2 0.8 [+ or -] 0.1 NA
 Npn3, neoplastic 1.0 [+ or -] 0.3 1.05
 progression protein-3

Cell cycle regulators
 and IGFs
 Cychn D1 4.8 [+ or -] 1.0 * 1.62 *
 Cyclin E 4.4 [+ or -] 1.5 * 1.19 *
 Cdk2na 7.1 [+ or -] 1.9 * 1.01
 Cdk2nb 2.3 [+ or -] 0.6 NA
 Cdk4 2.5 [+ or -] 0.5 1.53 *
 PCNA 2.5 [+ or -] 0.8 1.73 *
 P16 0.6 [+ or -] 0.2 0.85
 IGF-1 0.7 [+ or -] 0.1 0.65 *
 IGF-2 3.3 [+ or -] 2.1 3.77 *
 IGFBP1 2.7 [+ or -] 0.5 * 1.15
 IGFBP3 2.9 [+ or -] 0.8 * 0.88
 IGFBP5 4.6 [+ or -] 1.5 * 0.94

Stress-related genes
 GST-alpha4 2.5 [+ or -] 0.6 * 1.94 *
 GST-mu 3.5 [+ or -] 0.8 * 1.54 *
 GST-theta 3.5 [+ or -] 0.8 * 1.14
 GST-pi 2.5 [+ or -] 0.6 * 2.23
 EGR1,early response 3.5 [+ or -] 0.8 * 1.24 *
 SOD-1 2.5 [+ or -] 0.6 * NA
 Ceruloplasmin 4.1 [+ or -] 1.0 * 1.02
 HO-1, heme oxygenase-1 1.0 [+ or -] 0.2 1.51 *
 MT-1 0.6 [+ or -] 0.3 0.50 *

Genes for metabolic
 CYP2A4 3.1 [+ or -] 0.9 * 1.05
 CYP2F2 1.0 [+ or -] 0.2 1.12
 CYP2B9 1.9 [+ or -] 0.6 0.85
 CYP2D9 5.3 [+ or -] 1.0 * 1.15 *
 CYP3A41 0.4 [+ or -] 0.2 0.55 *
 CYP7B1 0.7 [+ or -] 0.3 0.82 *
 Akr1c18, aldo-keto 2 5 [+ or -] 0.8 1.39
 reductase 1cl8
 HSD1707 3.1 [+ or -] 0.4 * 0.92
 TFF3, trefoil factor 3 3.2 [+ or -] 1.0 * 5.82 *
 Cyr61, cysteine-rich 1.7 [+ or -] 0.3 0.85
 protein 61
 Lp1, lipoprotein lipase 12.1 [+ or -] 5.1 * 4.61
 Cte1, cytosolic acyl-CoA 2.7 [+ or -] 0.8 1.29 *
 Pmsc3 proteasome 26S 2.6 [+ or -] 0.4 1.62 *
 subunit, ATPase3
 BHMT, homocysteine 0.7 [+ or -] 0.1 0.84 *
 Saa3, serum amyloid 3 2.2 [+ or -] 0.7 0.23 *
 SULT-X2 0.1 [+ or -] 0.0 * 0.21 *

Cell communication and
 signal transduction
 Annexin A2 9.0 [+ or -] 2.9 * 2.30 *
 Nid1, nidogen 1 3.1 [+ or -] 1.1 2.60 *
 [beta]-catenin 4.2 [+ or -] 0.8 * 2.01 *
 E-cadherin 4.4 [+ or -] 1.5 * 1.24 *
 Ptgs-2, prostaglandin- 2.6 [+ or -] 1.0 1.12
 endoperoxidesynthase 2
 Rhou, ras homolog gene 3.1 [+ or -] 0.8 * NA
 family U
 CTGF, fibronectin 2.7 [+ or -] 0.6 2.50 *
 Prlr, prolactin receptor 0.4 [+ or -] 0.2 0.37 *
 Eafr, enidermal orowth 1.1 [+ or -] 0.2 0.71 *
 factor receptor

Gene categories (a) PCR Array-fold

Oncogenes and HCC-related
 alpha-fetoprotein 19.1 [+ or -] 5.4 * NA
 c-myc 3.1 [+ or -] 0.5 * 2.36 *
 c-met 3.4 [+ or -] 0.8 * 1.26 *
 K-ras 2.5 [+ or -] 0.6 * 1.54 *
 PAI-1, plasminogen 9.2 [+ or -] 2.9 * NA
 activator inhibitor-1
 Cytokeratin-8 6.0 [+ or -] 1.3 * NA
 Cytokeratin-18 2.9 [+ or -] 0.4 * 2.34 *
 Cytokeratin-19 11.1 [+ or -] 5.4 * 1.24
 BRCA1 0.4 [+ or -] 0.1 * 0.81 *
 BRCA2 0.7 [+ or -] 0.1 * NA
 Npn3, neoplastic 3.1 [+ or -] 0.8 * 2.41 *
 progression protein-3

Cell cycle regulators
 and IGFs
 Cychn D1 5.1 [+ or -] 0.9 * 1.51 *
 Cyclin E 5.2 [+ or -] 1.3 * 1.31 *
 Cdk2na 13.9 [+ or -] 3.8 * 1.20
 Cdk2nb 6.3 [+ or -] 1.8 * NA
 Cdk4 4.4 [+ or -] 0.2 * 1.76 *
 PCNA 2.6 [+ or -] 0.5 * 1.76 *
 P16 0.6 [+ or -] 0.1 * 0.83 *
 IGF-1 0.6 [+ or -] 0.1 * 0.53
 IGF-2 4.4 [+ or -] 2.0 * 4.21 *
 IGFBP1 9.1 [+ or -] 3.2 * 4.18 *
 IGFBP3 2.9 [+ or -] 0.8 * 0.88
 IGFBP5 2.4 [+ or -] 0.9 * 0.91

Stress-related genes
 GST-alpha4 2.5 [+ or -] 0.6 * 2.16 *
 GST-mu 4.8 [+ or -] 1.1 * 1.26 *
 GST-theta 3.1 [+ or -] 0.9 * 1.31
 GST-pi 2.5 [+ or -] 0.6 * 1.11
 EGR1,early response 3.1 [+ or -] 0.9 * 5.20 *
 SOD-1 2.5 [+ or -] 0.6 * NA
 Ceruloplasmin 4.3 [+ or -] 1.5 * 1.14 *
 HO-1, heme oxygenase-1 0.9 [+ or -] 0.2 1.23 *
 MT-1 0.5 [+ or -] 0.1 * 0.59 *

Genes for metabolic
 CYP2A4 25.3 [+ or -] 8.7 * 2.51 *
 CYP2F2 0.5 [+ or -] 0.2 * 0.68 *
 CYP2B9 2.6 [+ or -] 1.1 * 0.43
 CYP2D9 4.7 [+ or -] 1.2 * 1.06
 CYP3A41 0.4 [+ or -] 0.1 * 0.57 *
 CYP7B1 0.5 [+ or -] 0.1 * 0.39 *
 Akr1c18, aldo-keto 61.7 [+ or -] 27.8 * 15.3 *
 reductase 1cl8
 HSD1707 2.8 [+ or -] 0.4 0.99
 TFF3, trefoil factor 3 6.3 [+ or -] 1.8 * 10.9 *
 Cyr61, cysteine-rich 4.9 [+ or -] 1.7 * 1.17
 protein 61
 Lp1, lipoprotein lipase 33.2 [+ or -] 13.1 * 9.21 *
 Cte1, cytosolic acyl-CoA 4.8 [+ or -] 1.8 * 2.18 **
 Pmsc3 proteasome 26S 4.1 [+ or -] 1.1 * 1.61
 subunit, ATPase3
 BHMT, homocysteine 0.6 [+ or -] 0.1 * 0.63 *
 Saa3, serum amyloid 3 0.3 [+ or -] 0.1 * 0.05 *
 SULT-X2 0.0 [+ or -] 0.0 * 0.16 *

Cell communication and
 signal transduction
 Annexin A2 48.5 [+ or -] 16.9 * 8.64 *
 Nid1, nidogen 1 56.2 [+ or -] 9.8 * 10.5 *
 [beta]-catenin 6.9 [+ or -] 2.4 * 2.03 *
 E-cadherin 11.2 [+ or -] 4.5 * 4.34 *
 Ptgs-2, prostaglandin- 5.6 [+ or -] 2.5 * 1.18
 endoperoxidesynthase 2
 Rhou, ras homolog gene 3.9 [+ or -] 1.0 * NA
 family U
 CTGF, fibronectin 3.7 [+ or -] 0.8 * 1.90 *
 Prlr, prolactin receptor 0.4 [+ or -] 0.1 * 0.23 *
 Eafr, enidermal orowth 0.5 [+ or -] 0.1 * 0.63 *
 factor receptor

NA, same gene access clone is not available.
Data are mean [+ or -] SEM of 5-7 individual animals.

* Gene names, symbols, and accession numbers are from GenBank

* Significantly different from controls p < 0.05.
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Title Annotation:Research
Author:Waalkes, Michael P.
Publication:Environmental Health Perspectives
Date:Mar 1, 2006
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