Chronic arsenic exposure and cardiac repolarization abnormalities with QT interval prolongation in a population-based study.
OBJECTIVE: The objective of this study was to assess the cardiac effects of arsenic by investigating QT interval alterations in a human population chronically exposed to arsenic.
METHODS: Residents in Ba Men, Inner Mongolia, have been chronically exposed to arsenic via consumption of water from artesian wells. A total of 313 Ba Men residents with the mean arsenic exposure of 15 years were divided into three arsenic exposure groups: low ([less than or equal to] 21 [micro]g/L), medium (100-300 [micro]g/L), and high (430-690 [micro]g/L). ECGs were obtained on all study subjects. The normal range for QTc (corrected QT) interval is 0.33-0.44 sec, and QTc [greater than or equal to] 0.45 sec was considered to be prolonged.
RESULTS: The prevalence rates of QT prolongation and water arsenic concentrations showed a dose-dependent relationship (p = 0.001). The prevalence rates of QTc prolongation were 3.9, 11.1, 20.6% for low, medium, and high arsenic exposure, respectively. QTc prolongation was also associated with sex (p < 0.0001) but not age (p = 0.486) or smoking (p = 0.1018). Females were more susceptible to QT prolongation than males.
CONCLUSIONS: We found significant association between chronic arsenic exposure and QT interval prolongation in a human population. QT interval may potentially be useful in the detection of early cardiac arsenic toxicity.
KEY WORDS: arsenic, cardiac repolarization, cardiovascular effects, drinking water, nail, QT prolongation. Environ Health Perspect 115:690-694 (2007). doi:10.1289/ehp.9686 available via http://dx.doi.org/ [Online 14 February 2007]
Arsenic is an element found in multiple compounds commonly encountered in the environment. Human exposure to inorganic and organic arsenicals may occur from a variety of sources including occupational, medical, and environmental (Lee and Fraumeni 1969; Watanabe et al. 2004; Westervelt et al. 2001). Whether from medical therapy (as with the use of arsenic trioxide in advanced malignancies) or malicious intent (as in acute poisoning), the cardiac effects of massive acute arsenic exposure are well documented (Hall and Harruff 1989; Little et al. 1990; Westervelt et al. 2001). Patients experiencing arsenic toxicity manifest profound abnormalities in repolarization of the heart, resulting in life-threatening malignant ventricular arrhythmias (Ohnishi et al. 2002; St. Petery et al. 1970). Although chronic arsenic exposure via drinking water with high arsenic concentrations has been associated with coronary disease, stroke, and peripheral vascular disease in humans (Navas-Acien et al. 2005; Wang et al. 2002), little is known about its effects on cardiac electrophysiologic properties in general populations experiencing chronic lower-dose arsenic exposure from environmental contamination.
The primary inorganic arsenic exposure in the human population is through ingestion of contaminated drinking water. Arsenic is widely present in natural waters, in the form of inorganic arsenite ([As.sup.III]) and arsenate ([As.sup.V]). After consumption, inorganic arsenic is converted to methylated derivatives. Although methylation of arsenic has been commonly considered a mechanism for detoxification, recent studies have shown that methylated trivalent arsenicals are more toxic than inorganic arsenic (DeMarini et al. 2003). There are no appropriate animal models available for investigating health effects of arsenic. In 2001, the U.S. Environmental Protection Agency (EPA) adopted the maximum contaminant level (MCL) of 10 [micro]g/L for arsenic in drinking water (U.S. EPA 2001). Significant uncertainties remain regarding mechanisms by which arsenic exerts a deleterious affect on the cardiovascular system, especially at low exposure levels.
The QT (time between initial deflection of QRS complex to the end of T wave) interval on the electrocardiogram (ECG) represents the duration of ventricular electrical systole including depolarization and repolarization. The QT interval varies with heart rate and is typically expressed in seconds or milliseconds in a corrected form (QTc). Several calculations have been used to correct the measurement based on heart rate, and the most commonly employed is the Bazett formula (Bazett 1920). The upper limit of normal for QTc is 0.44 sec (Surawicz and Knilans 2001). Women are known to have slightly longer average QTc intervals than men (0.41 sec for women vs. 0.39 sec for men) (Chou 1986). Prolongation of the QTc intervals [greater than or equal to] 0.45 sec is associated with increased risk of arrhythmia and mortality. Wu et al. (2003) reported that the mean of the normal QTc interval for Chinese is 0.41 sec (0.42 sec for females and 0.40 sec for males).
Inner Mongolia is an autonomous region in Northern China. The study site is in the Bayingnormen (Ba Men) region located in Western Inner Mongolia on the Hetao Plain, north of the Huang He River (Figure 1). Before installation of the artesian wells in 1980, Ba Men residents used the water from the large shallow wells containing low levels of arsenic for drinking water. Since 1980, > 300,000 Ba Men residents used artesian wells and have been chronically exposed by drinking arsenic-contaminated water. Arsenic occurs naturally in ground water in Ba Men, in levels ranging from nondetectable to 1.8 mg/L (Ma et al. 1999). The counties in Ba Men most affected by arsenicosis are Lin He, Wu Yuan, and Hangjin Hou (Figure 1). Health effects, including dermal (skin hyperkeratosis, alterations in pigmentation, and cancer), neurologic, cardiovascular, and peripheral vascular diseases have been reported in this region (Ma et al. 1999). Ba Men residents have been exposed to a wide range of arsenic concentrations, and it is possible to assess individual exposure because most households (80%) have their own wells. This region is known for its abundance of agricultural products, including dairy and domestic animals for both commercial and personal consumption. In general, nutrition is not a problem among the residents. In Ba Men, drinking water is the main source of arsenic intake. Chinese investigations on arsenic contamination in Ba Men region have shown that the levels of arsenic in the irrigation or surface water from Huang He River are below the U.S. standard for arsenic in drinking water, ranging from 2 to 9 [micro]g/L (Yu et al. 1995). Therefore, arsenic concentrations in grains, beans, poultry, vegetables, and fruits are low. Occasionally, the residents consume freshwater fish or shrimp, but most residents ([greater than or equal to] 60%) do not (Table 1). Thus, intake from diet in this population is not an important source of arsenic exposure. Because migration in this region is minimal among Ba Men residents, and for the reasons stated above, this population provided good opportunities for assessing cardiovascular effects of chronic arsenic exposure in humans. The objective of the study was to assess the effects of chronic exposure to arsenic on cardiac repolarization by investigating ECG QT intervals in a general population.
Materials and Methods
Study subjects. Because little information is available on the effects of chronic arsenic exposure via drinking water on QT interval in a general population, we conducted a range-finding study. Study subjects had been exposed to a wide range of arsenic levels (low, medium, and high with gaps among the groups), so we investigated at what levels, if any, arsenic exposure affected QT interval in this population. The study subjects included 313 residents of the Ba Men region exposed to different levels of arsenic concentrations via drinking water. One ECG was collected from each subject. Among the 313 ECGs, three manifested right bundle branch block. These subjects were excluded from the data analysis of QT interval. The low-exposed subjects were from the village of Long Sheng in Lin He County, the medium-exposed from Gu Cheng in Lin He County and Yong Li in Wu Yuan County, and the high-exposed were from Fen Zi Di in Lin He County (Figure 1).
We obtained information regarding the consumption of artesian well water with arsenic contamination, tobacco smoking, alcohol consumption, sociodemographic characteristics, and past medical history through questionnaires (Table 1). This study was conducted according to the recommendations of the Declaration of Helsinki (World Medical Association 1989) for international health research. All subjects gave written informed consents to participate in this study. The research protocol met the requirements for protection of human subject certification and was approved by the U.S. EPA.
Arsenic exposure assessment. Water collection and arsenic analysis. Samples of drinking water were collected in acid-washed containers from the study subjects' homes, as previously described (Mo et al. 2006). Drinking-water samples from the storage tank for well water in each home were collected, stored at -20[degrees]C, and transported on ice via air to University of Alberta in Edmonton, Canada, for analysis. Total arsenic was determined using hydride generation atomic fluorescence spectrometry (HGAFS) (Le and Ma 1998). The detection limit for HGAFS is 0.2 [micro]g/L.
Nail collection and analysis. Toenail arsenic has been reported to provide an integrated measure of internal arsenic exposure (Karagas et al. 1996). In this study, toenail samples were collected from each study subject as described previously and transported to the U.S. EPA laboratory in Research Triangle Park, North Carolina, for analysis (Schmitt et al. 2005). The nail samples were cleaned by sonification in HPLC-grade water and then acetone washed to remove debris from the nail surface. Toenails were analyzed for arsenic using Instrumental Neutron Activation Analysis (INAA) at North Carolina State University Nuclear Services Department (Raleigh, NC, USA) (Heydorn 1984). The detection limit for INAA is 0.0012 [micro]g/g.
QT measurement and evaluation. The ECG QT interval defines the period of ventricular repolarization. The subjects were placed in a supine position. After 10 min of rest, an ECG tracing was recorded for 2 min. In this study, two cardiologists (W.E.S., J.F.) who are certified as electrophysiologists by the American Board of Internal Medicine measured all QT intervals. Discrepancies in the measurement of QT interval between the two cardiologists who evaluated the ECGs were rare. In cases where the measurements were not the same, an average was used. Heart rate of each subject was also determined from the ECG. The physicians were blinded to subjects' arsenic level as well as the other physician's interpretation of the ECG. QT interval was corrected for heart rate using the Bazett formula (Bazett 1920). A QTc interval of [less than or equal to] 0.44 sec was considered normal.
Statistical analysis. Arsenic concentration was divided into three categories: low (< 21 [micro]g/L), medium (100-350 [micro]g/L), and high (430-690 [micro]g/L). Age was also divided into three categories: young (9-29 years), middle aged (30-50 years), and older (51-65 years). We assessed exposure by measuring arsenic concentrations in drinking water and nails. QTc interval was considered to be normal if it was [less than or equal to] 0.44 sec and abnormal if it was [greater than or equal to] 0.45 sec. We performed analysis of Spearman correlation coefficients to evaluate the association between arsenic concentrations in drinking water and nails. We compared heart rate and QTc interval measurements in subgroups using Student's t-test. We evaluated bivariate associations between categorical variables using chi-square tests. We used a binary logistic regression model with the QTc interval as dependent outcome and arsenic concentration as the predictor of interest. After prior selection, we used age, sex, smoking status, body mass index (BMI), and pesticide exposure as control covariates in the model. Also two-by-two interactions of the above six main effects are included in the model to control for possible interactions. We used the maximum likelihood estimation method to estimate the logistic model (Hosmer and Lemeshow 2000). The main effects model was fit with all the main effects including age, sex, smoking, BMI, and pesticide exposure. For the final model, we used backward selection with the main effects and all two-way interactions in the full model, eliminating the least significant terms at each iteration and including only the statistically significant variables (p < 0.05) in the final model. The final-selected variables maximize the likelihood of distribution of QTc interval outcome and thus significantly predict the QTc interval outcome. All statistical analyses were conducted using SAS version 9.1 (SAS Institute Inc., Cary, NC, USA).
Study subjects. Table 1 shows the characteristics of the study subjects. Most of the subjects were farmers with an average of 15 years of chronic arsenic exposure. There were a total of 168 males and 145 females with a mean age of 35 [+ or -] 14 years; among these subjects, 33% were smokers. Most subjects had at least a primary education. Diet included frequent meat, fruits, and vegetables. Vitamin use was rare ([less than or equal to] 2%). Most subjects did not consume seafood from fresh water, or if they did, it was infrequent.
Water and nail arsenic concentrations. Table 2 shows the nail arsenic concentrations in the low, medium, and high arsenic exposure groups. The mean arsenic concentrations in nails and drinking water in these study subjects showed a positive dose-dependent relationship. Arsenic concentrations in nails and water showed positive correlations in all three groups and also in all subjects.
QTc and arsenic exposure. Figure 2 shows the effects of arsenic, age, sex, and smoking on QTc interval. Significant dose-related prevalence rates of QT prolongation were seen in the subjects with increasing water arsenic concentrations (p = 0.001) and was most profound in the high-exposure group, with 20.6% of the subjects having marked cardiac repolarization abnormalities. Medium arsenic exposure resulted in 11.1% of subjects having QTc prolongation. The low arsenic exposure group had QTc abnormalities in 3.9% of study subjects. Using chi-square tests, we observed no statistically significant differences in the prevalence of QTc prolongation related to tobacco smoking (p = 0.1018) or age (p = 0.486). However, there was a significant difference due to sex (p = 0.0001). Females were more susceptible to QT interval prolongation than males.
Results from maximum likelihood estimation of logistic regression models, including main effects model and the final model are shown in Table 3. The main effects model controlled for arsenic exposure, age, sex, smoking, BMI, and pesticide exposure; the final model controlled for arsenic exposure, age, sex, BMI, and age-BMI interaction. The results from the main effects model showed that prolonged QTc was associated with arsenic exposure and sex, but not age, smoking, or pesticide exposure. This is consistent with the results from the chi-square tests shown above. Smoke and pesticide exposure were dropped out of the final model. Also dropped out of the final model were all other insignificant interactions except age-BMI interaction, which was statistically significant (p < 0.0020). For lower-level BMI, as age increased, the probability of prolonged QTc interval tends to decrease, and for upper-level BMI, as age increased the probability of prolonged QTc interval tends to increase. Both the main effects and the final model showed a dose-dependent relationship in increasing odds ratio (OR) between arsenic concentrations and prolonged QTc intervals (Table 4). In the final model, although all other covariates remain constant, the adjusted OR of prolonged QTc interval for the medium- versus low-exposure group was 3.829 [95% confidence interval (CI), 1.128-12.993] and the high- versus low-exposure group was 8.848 (95% CI, 2.723-28.748). Sex was also a significant predictor, with OR of 5.819 (95% CI, 2.486-13.621) for female versus male.
Heart rates and QTc. Table 5 shows the comparison of heart rate and QTc interval in the QTc prolonged and normal subjects. The individual withs prolonged QTc demonstrated a statistical significant increase in heart rate in the medium- and high-exposure groups, but not in the low-exposure group. Arsenic has known effects on the nervous system (Hindmarsh et al. 1977). In this study, the subjects with prolonged QTc had slightly higher normal baseline heart rates. This may reflect the arsenic effects on the autonomic nervous system with withdrawal of parasympathetic tone to the sinus node. In Table 5, the mean QTc interval for the low-exposure group was 0.41 sec, which is consistent with the mean of the reported normal QTc for Chinese subjects (Wu et al. 2003). There were statistical differences in QTc measurements between the prolonged QTc and normal individuals.
Chronic arsenic exposure has long been associated with carcinogenesis and atherogenesis, particularly peripheral vascular disease (Simeonova and Luster 2004; Yoshida et al. 2004). Increased mortality from cardiovascular events in individuals in Taiwan who were exposed to arsenic via artesian wells has been reported (Chen et al. 1996). Although Ahmad et al. (2006) reported a study conducted in Bangladesh showing significant difference in QTc interval between the arsenicosis and the non-arsenic-exposed group, cardiac repolarization abnormalities showing dose-dependent relationship with arsenic exposure has not been previously observed. In this study, we evaluated ECG changes in individuals exposed to arsenic via drinking water in Inner Mongolia and assessed the association of prolongation of QTc interval with environmental arsenic exposure. A dose-response relationship was observed, and the prevalence of prolonged QTc interval was significantly associated with arsenic exposure via drinking water in this general population in Inner Mongolia. This is in agreement with the clinical studies showing that arsenic trioxide used in the treatment of acute promyelocytic leukemia induced significant cardiac electrophysiologic abnormalities (QT prolongation) and ventricular arrhythmias (torsade de pointes) (Westervelt et al. 2001). Similar cardiac electrical changes have been shown in acute arsenic poisoning (St. Petery et al. 1970).
The mechanisms by which arsenic induces QT interval prolongation are not completely understood. We hypothesize that this might be caused by the functional alterations in cardiac cell surface channels. Potassium-selective channels play a key role in maintaining the resting membrane potential and repolarization of the action potential in excitable cardiac myocytes (Sanguinetti and Tristani-Firouzi 2006). Hereditary QT prolongation or long QT syndrome occurs in patients with mutations in the cardiac ion channel genes, particularly those involved in potassium ion flow (Keating and Sauguinetti 2001). Among the potassium channel genes, the most commonly observed inherited mutations are found in hERG (the human ether-a go-go-related gene) and KCNQ1 (Curran et al. 1995; Wang et al. 1996). These channelopathies result in significant alterations in cardiac repolarization and predispose the affected individuals to arrhythmias and sudden cardiac death (Sanguinetti and Tristani-Firouzi 2006). hERG encodes the voltage-gated potassium channel [alpha] subunit underlying [I.sub.kr] (rapidly activating potassium current) (Sanguinetti et al 1995). Potassium current change can result from blockade of the potassium channel, alterations of ion selectivity, or reduction of hERG protein expression. Proarrhythmia is observed in patients treated with drugs that block the hERG channel, including quinidine, dofetilide, antihistamines, and antibiotics (Bednar et al. 2001; Redfern et al. 2003). In addition, the therapeutic use of arsenic trioxide in the treatment of acute promyelocytic leukemia has been hampered by its severe side effects, which include QT prolongation, malignant ventricular tachycardia (torsade de pointes), and sudden death (Unnikrishnan et al. 2001). Recently, arsenic trioxide has been shown to block [I.sub.kr] by inhibition of the processing of the hERG protein in the endoplasmic reticulum (Ficker et al. 2004). In contrast to other drugs, which result in blockade via binding to specific sites within the channel, arsenic trioxide appears to produce hERG liability by inhibition of ion-channel trafficking resulting in reduced channel expression on the cell surface. The QT prolongation seen in our study is most probably the consequence of potassium ion channel alterations induced by arsenic, and may involve hERG trafficking defects.
In this study we observed that age and smoking were not important factors in QT prolongation. However, there was a significant difference related to sex. Women showed an increased sensitivity to toxic effects of arsenic with regard to QT prolongation. Women are known to exhibit average QT intervals slightly longer than those of men and are also more susceptible to the drugs that induce prolonged QT (Drici et al. 1998; Lehmann et al. 1996; Villareal et al. 2001). This may explain the higher frequency of QT interval prolongation in women exposed to arsenic. We are conducting a follow-up study with a larger sample size focusing on women and the sex-specific effects of arsenic as manifested by QT prolongation. Our finding that chronic inorganic arsenic ingestion in a general population can result in QT prolongation may help explain the increased cardiovascular mortality in humans exposed to contaminated drinking water. The risk of significant arrhythmia increases with an increasing QT interval, but is still present with minimal prolongation. In summary, we found significant association between chronic arsenic exposure and QT interval prolongation in a human population, and ECG analysis of the QT interval may be useful in detecting early cardiac arsenic toxicity and in evaluating populations at risk for cardiovascular events. In addition to a larger follow-up study investigating arsenic effects on QT prolongation, we are also conducting a study to investigate cardiac morbidity and mortality in this population. The Chinese government recently has provided assistance in installing water systems in Ba Men to lower the arsenic levels in well water among the Ba Men residents. Reducing arsenic concentrations in drinking water to a safe level in this population would likely eliminate QT prolongation and the associated cardiac risk.
Ahmad SA, Khatun F, Sayed MH, Khan MH, Aziz R, Hossain MZ, et al. 2006. Electrocardiographic abnormalities among arsenic-exposed persons through groundwater in Bangladesh. J Health Popul Nutr 24:221-227.
Bazett HC. 1920. An analysis of the time-relations of electrocardiograms. Heart 7:353-370.
Bednar MM, Harrigan EP, Anziano RJ, et al. 2001. The QT interval. Prog Cardiovasc Dis 43:1-45.
Chen CJ, Chiou HY, Chiang MH, Lin LJ, Tai TY. 1996. Dose-response relationship between ischemic heart disease mortality and long-term arsenic exposure. Arterioscler Thromb Vasc Biol 16:504-510.
Chou T. 1986. Electrocardiography in Clinical Practice. 2nd ed. Philadelphia:W.B. Saunders Company.
Curran ME, Splawski I, Timothy KW, Vincent GM, Green ED, Keating MT. 1995. A molecular basis for cardiac arrhythmia: HERG mutations cause long QT syndrome. Cell 80:795-803.
DeMarini DM, Kligerman AD, Doerr CL, Tennant AH, Harrington-Brock K, Allen JW, et al. 2003. Methylated trivalent arsenicals as candidate ultimate genotoxic forms of arsenic: induction of chromosomal mutations but not gene mutations. Environ Mol Mutagen 42:192-205.
Drici MD, Knollmann BC, Wang WX, Woosley RL. 1998. Cardiac actions of erythromycin: influence of female sex. JAMA 280:1774-1776.
Ficker E, Kuryshev YA, Dennis AT, Obejero-Paz C, Wang L, Hawryluk P, et al. 2004. Mechanisms of arsenic-induced prolongation of cardiac repolarization. Mol Pharmacol 66:33-44.
Hall JC, Harruff R. 1989. Fatal cardiac arrhythmia in a patient with interstitial myocarditis related to chronic arsenic poisoning. South Med J 82:1557-1560.
Heydorn K. 1984. Analysis. In: Neutron Activation Analysis for Clinical Trace Element Research, Vol 1. Boca Raton, FL:CRC Press, 73-165.
Hindmarsh J, McLetchie O, Hefferman L, Hayne O, Ellenberger H, McCurdy R, Thiebaux T. 1977. Electromyographic abnormalities in chronic environmental arsenicalism. J Anal Toxicol 1:270-276.
Hosmer DW, Lemeshow S. 2000. Applied Logistic Regression. 2nd ed. New York:Wiley, Inc.
Karagas MR, Morris JS, Weiss JE, Spate V, Baskett C, Greenberg ER. 1996. Toenail samples as an indicator of drinking water arsenic exposure. Cancer Epidemiol Biomarkers Prev 5:849-852.
Keating MT, Sanguinetti MC. 2001. Molecular and cellular mechanisms of cardiac arrhythmias. Cell 104:569-580.
Le XC, Ma M. 1998. Short-column liquid chromatography with hydride generation atomic fluorescence detection for the speciation of arsenic. Anal Chem 70:1926-1933.
Lee AM, Fraumeni JF Jr. 1969. Arsenic and respiratory cancer in man: an occupational study. J Natl Cancer Inst 42:1045-1052.
Lehmann MH, Hardy S, Archibald D, Quart B, MacNeil DJ. 1996. Sex difference in risk of torsade de pointes with d,l-Sotalol. Circulation 94:2535-2541.
Little RE, Kay GN, Cavender JB, Epstein AE, Plumb VJ. 1990. Torsade de pointes and T-U wave alternans associated with arsenic poisoning. Pacing Clin Electrophysiol 13:164-170.
Ma HZ, Xia YJ, Wu KG, Sun TZ, Mumford JL. 1999. Human exposure to arsenic and health effects in Bayingnormen, Inner Mongolia. In: Arsenic Exposure and Health Effects (Chappell WR, Abernathy CO, Calderon RL, eds). Amsterdam:Elsevier, 127-131.
Mo J, Xia Y, Wade T, Schmitt M, Le XC, Dang R, et al. 2006. Chronic arsenic exposure and oxidative stress: OGG1 expression and arsenic exposure, nail selenium, and skin hyperkeratosis in Inner Mongolia. Environ Health Perspect 114:835-841.
Navas-Acien A, Sharrett AR, Silbergeld EK, Schwartz BS, Nachman KE, Burke TA, et al. 2005. Arsenic exposure and cardiovascular disease: a systematic review of the epidemiologic evidence. Am J Epidemiol 162:1037-1049.
Ohnishi K, Yoshida H, Shigeno K, Nakamura S, Fujisawa S, Naito K, et al. 2002. Arsenic trioxide therapy for relapsed or refractory Japanese patients with acute promyelocytic leukemia: need for careful electrocardiogram monitoring. Leukemia 16:617-622.
Redfern WS, Carlsson L, Davis AS, Lynch WG, MacKenzie I, Palethorpe S, et al. 2003. Relationships between preclinical cardiac electrophysiology, clinical QT interval prolongation and torsade de pointes for a broad range of drugs: evidence for a provisional safety margin in drug development. Cardiovasc Res 58:32-45.
Sanguinetti MC, Jiang C, Curran ME, Keating MT. 1995. A mechanistic link between an inherited and an acquired cardiac arrhythmia: HERG encodes the IKr potassium channel. Cell 81:299-307.
Sanguinetti MC, Tristani-Firouzi M. 2006. HERG potassium channels and cardiac arrhythmia. Nature 440:463-469.
Schmitt MT, Schreinemachers D, Wu K, Ning Z, Zhao B, Le XC, et al. 2005. Human nails as a biomarker of arsenic exposure from well water in Inner Mongolia: comparing atomic fluorescence spectrometry and neutron activation analysis. Biomarkers 10:95-104.
Simeonova PP, Luster MI. 2004. Arsenic and atherosclerosis. Toxicol Appl Pharmacol 198:444-449.
St. Petery J, Gross C, Victorica BE. 1970. Ventricular fibrillation caused by arsenic poisoning. Am J Dis Child 120:367-371.
Surawicz and Knilans. 2001. Normal electrocardiogram: origin and description. In: Chou's Electrocardiography in Clinical Practice (Surawicz B, Knilant T, eds). Philadelphia:W.B. Saunders, 3-27.
Unnikrishnan D, Dutcher JP, Varshneya N, Lucariello R, Api M, Garl S, et al. 2001. Torsades de pointes in 3 patients with leukemia treated with arsenic trioxide. Blood 97:1514-1516.
U.S. EPA (U.S. Environmental Protection Agency). 2001. National Primary Drinking Water Regulations: Arsenic and Clarifications to Compliance and New Source Contaminants Monitoring. 40 CFR Parts 141 and 142. Fed Reg 66(19):50961.
Villareal RP, Woodruff AL, Massumi A. 2001. Gender and cardiac arrhythmias. Tex Heart Inst J 28:265-275.
Wang CH, Jeng JS, Yip PK, Chen CL, Hsu LI, Hsueh YM, et al. 2002. Biological gradient between long-term arsenic exposure and carotid atherosclerosis. Circulation 105:1804-1809.
Wang Q, Curran ME, Splawski I, Burn TC, Millholland JM, VanRaay TJ, et al. 1996. Positional cloning of a novel potassium channel gene: KVLQT1 mutations cause cardiac arrhythmias. Nat Genet 12:17-23.
Watanabe C, Kawata A, Sudo N, Sekiyama M, Inaoka T, Bae M, et al. 2004. Water intake in an Asian population living in arsenic-contaminated area. Toxicol Appl Pharmacol 198:272-282.
Westervelt P, Brown RA, Adkins DR, Khoury H, Curtin P, Hurd D, et al. 2001. Sudden death among patients with acute promyelocytic leukemia treated with arsenic trioxide. Blood 98:266-271.
World Medical Association. 1989. Declaration of Helsinki. Available: http://www.wma.net/e/policy/b3.htm [accessed 19 March 2007].
Wu J, Kors JA, Rijnbeek PR, van Herpen G, Lu Z, Xu C. 2003. Normal limits of the electrocardiogram in Chinese subjects. Int J Cardiol 87:37-51.
Yoshida T, Yamauchi H, Fan Sun G. 2004. Chronic health effects in people exposed to arsenic via the drinking water: doseresponse relationships in review. Toxicol Appl Pharmacol 198:243-252.
Yu GJ, Ma HZ, Wu KG, Xia YJ, Li YH, Zheng Z, et al. 1995. Investigations of environmental arsenic in arsenicism endemic area of Inner Mongolia. Chin J Epidemiol (special supplement Endemic Arsenic Poisoning) September:10-14.
Judy L. Mumford, (1) Kegong Wu, (2) Yajuan Xia, (2) Richard Kwok, (3) Zhihui Yang, (4) James Foster, (5) and William E. Sanders Jr. (6,7)
(1) U.S. Environmental Protection Agency, National Health and Environmental Effects Research Laboratory, Research Triangle Park, North Carolina, USA; (2) Inner Mongolia Center for Endemic Disease Control and Research, Huhhot, Inner Mongolia, China; (3) RTI International, Research Triangle Park, North Carolina, USA; (4) Ba Men Anti-Epidemic Station, Lin He, Inner Mongolia, China; (5) Wake Heart Associates, Raleigh, North Carolina, USA; (6) Department of Medicine, and (7) Center for Environmental Medicine, Asthma and Lung Biology, University of North Carolina, Chapel Hill, North Carolina, USA
Address correspondence to J.L. Mumford, MD 58C, U.S. Environmental Protection Agency, Research Triangle Park, NC 27711 USA. Telephone: (919) 966-0651. Fax: (919) 966-0655. Email: firstname.lastname@example.org
We thank I.I.H. Chen for his technical advice in preparing this manuscript, X.C. Le of the University of Alberta for analyzing water samples, S. Lassell of North Carolina State University for analyzing nail samples, Y. Li of RTI International for excellent assistance in statistical analysis, and also all the participating members of Inner Mongolia Center for Endemic Disease Control and Research and Ba Men Anti-epidemic Station.
This research has been reviewed by the U.S. EPA and approved for publication. Approval does not signify that the contents reflect views of the agency or endorse the trade names mentioned.
This study was conducted and funded by the U.S. EPA, partially funded by Cooperative Agreement R82952201 with the University of North Carolina at Chapel Hill, Center for Environmental Medicine, Asthma and Lung Biology; and Cooperative Agreement R82808401, Inner Mongolia Center for Endemic Disease Control and Research.
The authors declare they have no competing financial interests.
Received 6 September 2006; accepted 14 February 2007.
Table 1. Study subjects' information, by low, medium, and high levels of arsenic. Medium Low (100-300 Characteristic (BDL-21 [micro]g/L) [micro]g/L) No. of subjects 103 108 Sex [no. (male/female)] 53/50 57/51 Age [years (mean [+ or -] SD)] 35 [+ or -] 14 36 [+ or -] 14 Smoker (%) 29 41 Education (%) Illiterate 13 19 Primary 41 49 Middle 39 26 High 7 6 Water arsenic concentration 10.7 [+ or -] 6.6 199.9 [+ or -] [[micro]g/L (mean [+ or -] SD)] 55.7 Water consumption (L/day) 1.6 [+ or -] 1.0 1.9 [+ or -] 1.1 Years of arsenic exposure 17.0 [+ or -] 3.4 14.6 [+ or -] (mean [+ or -] SD) 3.5 Pesticide exposure within 60 53 previous 5 years (% yes) Diet Meat [> 3 times/week (%)] 100 97 Fruit/vegetables [> 3 times/ 100 98 week (%)] Seafood (%) Do not eat 60 72 [less than or equal to] 1 40 28 time/week [greater than or equal to] 3 0 0 times/week BMI (a) 22.9 [+ or -] 3.7 22.7 [+ or -] 3.4 Alcohol consumption [> 2 times/ 22 15 week (% yes)] High Characteristic (430-690 [micro]g/L) No. of subjects 102 Sex [no. (male/female)] 58/44 Age [years (mean [+ or -] SD)] 34 [+ or -] 14 Smoker (%) 30 Education (%) Illiterate 18 Primary 42 Middle 37 High 3 Water arsenic concentration 568.3 [+ or -] 71.1 [[micro]g/L (mean [+ or -] SD)] Water consumption (L/day) 1.9 [+ or -] 1.2 Years of arsenic exposure 14.7 [+ or -] 3.3 (mean [+ or -] SD) Pesticide exposure within 50 previous 5 years (% yes) Diet Meat [> 3 times/week (%)] 100 Fruit/vegetables [> 3 times/ 98 week (%)] Seafood (%) Do not eat 60 [less than or equal to] 1 38 time/week [greater than or equal to] 3 2 times/week BMI (a) 22.6 [+ or -] 3.1 Alcohol consumption [> 2 times/ 12 week (% yes)] Abbreviations: BDL, below detection limit; BMI, body mass index. (a) BMI was calculated as body weight (kg) divided by squared body height ([m.sup.2]). Table 2. Nail arsenic concentrations and correlations between toenails and water arsenic concentrations. Nail arsenic concentration [[micro]g/g (mean [+ or -] Water arsenic exposure No. SD)] Spearman r p-Value All subjects 307 (a) 11.80 [+ or -] 0.9056 < 0.0001 11.80 Low exposure (< 21 103 1.21 [+ or -] 0.3478 0.0003 [micro]g/L) 0.74 Medium exposure (100-300 102 9.79 [+ or -] 0.3547 0.0003 [micro]g/L) 4.77 High exposure (430-690 102 24.61 [+ or -] 0.3940 < 0.0001 [micro]g/L) 10.65 (a) Data were missing from six subjects. Table 3. Analysis of maximum likelihood estimates from binary logistic regression models. Parameter Estimate SE p-Value Main effects model (a) Water arsenic (medium vs. low exposure) 1.1184 0.6083 0.0660 Water arsenic (high vs. low exposure) 1.9706 0.5814 0.0007 Age 0.00354 0.0168 0.8328 Sex 1.5678 0.5311 0.0032 Smoking 0.3363 0.5536 0.5436 BMI -0.0558 0.0652 0.3921 Pesticide exposure -0.3462 0.4580 0.4498 Constant -2.9943 1.4464 0.0384 Final model (b) Water arsenic (medium vs. low exposure) 1.3426 0.6234 0.0313 Water arsenic (high vs. low exposure) 2.1802 0.6012 0.0003 Age -0.2524 0.0835 0.0025 Sex 1.7611 0.4340 < 0.0001 BMI -0.5237 0.1701 0.0021 Age/BMI interaction 0.0123 0.00398 0.0020 Constant 6.0435 3.2398 0.0621 (a) Main effects model adjusting for arsenic, age, sex, tobacco smoking, BMI, and pesticide exposure. (b) Final model adjusting for arsenic, age, sex, BMI, and age/BMI interaction. Table 4. Estimated ORs (95% CIs) for relationships between QTc intervals and arsenic exposure. Water arsenic exposure Main effects model (a) Final model (b) Low exposure (reference 1.0 1.0 group) Medium vs. low exposure 3.060 (0.929-10.081) 3.829 (1.128-12.993) High vs. low exposure 7.175 (2.296-22.425) 8.848 (2.723-28.748) (a) Main effects model adjusting for arsenic, age, sex, tobacco smoking, BMI, and pesticide exposure. (b) Final model adjusting for arsenic, age, sex, BMI, and age/BMI interaction. Table 5. Heart rate and QTc among the subjects with prolonged QTc and normal QTc subjects (mean [+ or -] SD). Water arsenic Heart rate exposure Subjects with QTc [less than or equal to] 0.44 sec (n) Low exposure 66 [+ or -] 10 (99) Medium exposure 68 [+ or -] 10 (96) High exposure 68 [+ or -] 10 (81) All Subjects 68 [+ or -] 10 (276) Heart rate Subjects with Water arsenic QTc [greater than or equal to] 0.45 exposure sec (n) p-Value (a) Low exposure 73 [+ or -] 13 (4) 0.1910 Medium exposure 80 [+ or -] 15 (12) 0.0194 High exposure 76 [+ or -] 10 (21) 0.0018 All Subjects 77 [+ or -] 12 (37) < 0.0001 Water arsenic QTc exposure Subjects with QTc [less than or equal to] 0.44 sec (n) Low exposure 0.409 [+ or -] 0.021 (99) Medium exposure 0.407 [+ or -] 0.021 (96) High exposure 0.410 [+ or -] 0.023 (81) All Subjects 0.409 [+ or -] 0.023 (276) QTc Water arsenic Subjects with exposure QTc [greater than or equal to] 0.45 sec (n) p-Value Low exposure 0.467 [+ or -] 0.016 (4) < 0.0001 Medium exposure 0.456 [+ or -] 0.017 (12) < 0.0001 High exposure 0.459 [+ or -] 0.017 (21) < 0.0001 All Subjects 0.459 [+ or -] 0.017 (37) < 0.0001 (a) p-Values are from t-tests.
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|Author:||Mumford, Judy L.; Wu, Kegong; Xia, Yajuan; Kwok, Richard; Yang, Zhihui; Foster, James; Sanders, Will|
|Publication:||Environmental Health Perspectives|
|Date:||May 1, 2007|
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