Review Volume 122 | Issue 7 | July 2014
Environ Health Perspect; DOI:10.1289/ehp.1307864
Mercury Exposure and Health Impacts among Individuals in the Artisanal and Small-Scale Gold Mining Community: A Comprehensive Review
Herman Gibb and Keri Grace O’Leary
Background: Mercury (Hg) is used in gold mining to extract gold from ore by forming “amalgam”—a mixture composed of approximately equal parts mercury and gold. Approximately 15 million people, including approximately 3 million women and children, participate in artisanal small-scale gold mining (ASGM) in developing countries. Thirty-seven percent of global air emissions of Hg are produced by ASGM. The recently adopted Minamata Convention calls for nations to gather health data, train health-care workers, and raise awareness in regard to ASGM activity.
Objective: The purpose of our review was to evaluate the current literature regarding the health effects of Hg among those working and/or living in or near ASGM communities.
Methods: We searched PubMed, ScienceDirect, and Google Scholar for studies relating to health effects and biomarkers of Hg exposure in ASGM communities. Articles published from 1990 through December 2012 were evaluated for relevance.
Discussion: Studies reporting health assessments, kidney dysfunction, neurological disorders and symptoms, and immunotoxicity/autoimmune dysfunction in individuals living in or near an ASGM community were identified. More than 60 studies that measured biomarkers of Hg exposure in individuals living in or near ASGM communities were also identified. These studies, conducted in 19 different countries in South America, Asia, and Africa, demonstrated that hair and urine concentrations are well above World Health Organization health guidance values in ASGM communities.
Conclusions: ASGM workers and their families are exposed to Hg vapor, and workers, workers’ families, and residents of nearby and downstream communities are consuming fish heavily contaminated with methylmercury.
Citation: Gibb H, O’Leary KG. 2014. Mercury exposure and health impacts among individuals in the artisanal and small-scale gold mining community: a comprehensive review. Environ Health Perspect 122:667–672; http://dx.doi.org/10.1289/ehp.1307864
Address correspondence to H. Gibb, 3033 Wilson Blvd., Suite 700, Arlington, VA 22201 USA. Telephone: (703) 647-4180. E-mail: email@example.com
We acknowledge E. Ryan and M. Piper for their assistance in the preparation of the manuscript.
H.G. and K.G.O. are both employed by Tetra Tech Sciences, Arlington, VA. This article was commissioned by the World Health Organization (WHO) with financial support from the German Ministry of Environment, Nature Conservation and Nuclear Safety.
The authors alone are responsible for the views expressed in this publication and they do not necessarily represent the decisions or policies of the WHO.
The authors declare they have no actual or potential competing financial interests.
Received: 8 November 2013
Accepted: 26 March 2014
Advance Publication: 28 March 2014
Final Publication: 1 July 2014
- Supplemental Material (433 KB) PDF
In February 2009, the Governing Council of the United Nations Environment Programme (UNEP) began development of a legally binding global instrument on mercury (Hg). In January 2013, governments agreed to text for this instrument, thus giving birth to the Minamata Convention on Mercury (UNEP 2013b). In October 2013, the convention was signed in Minamata, Japan. Article 7 and Annex C of the convention address artisanal and small-scale gold mining (ASGM) and the development of national plans for ASGM. Included in the outline for national plans is development of a public health strategy on the exposure of artisanal and small-scale gold miners and their communities to Hg. Such a strategy should include the gathering of health data, training for health-care workers, and raising awareness through health facilities.
Hg is used in gold mining to extract gold from ore by forming “amalgam”—a mixture composed of approximately equal parts Hg and gold [Arctic Monitoring and Assessment Programme (AMAP)/UNEP 2013]. The amalgam is heated, evaporating the Hg from the mixture, leaving the gold (AMAP/UNEP 2013). This method of gold extraction is used in the ASGM community because it is cheaper than most alternative methods, can be used by one person independently, and is quick and easy (UNEP 2012). The dramatic rise in the cost of gold over the last decade has fueled a gold rush by poverty-driven miners in many countries (UNEP 2008). ASGM occurs primarily in South America, Africa, and Asia, but it can also be found in North America and Australia (UNEP 2013c). Approximately 15 million people, including approximately 3 million women and children, participate in the ASGM industry in 70 countries (UNEP 2012). ASGM is the largest source (37%) of global Hg emissions (UNEP 2013c). Between 2005 and 2010, Hg emissions from ASGM doubled (UNEP 2013a). Although most uses of Hg are declining throughout the world, the ASGM demand for Hg is expected to increase (UNEP 2013c). ASGM accounts for the largest percentage of global Hg demand (UNEP 2013c).
Hg vapors in the air around amalgam burning sites can be alarmingly high and almost always exceed the World Health Organization (WHO) limit for public exposure of 1.0 μg/m3 (UNEP 2012). These exposures affect not only the workers but also those in the communities surrounding the processing centers (UNEP 2012). Drake et al. (2001) reported that the range of the 8-hr time-weighted average airborne Hg exposure at gold mining operations in Venezuela was 0.1–6,315 μg/m3 with a mean of 183 μg/m3. The WHO (2000) reported that tremor has been observed in workers exposed to 30 μg/m3 Hg and that renal tubular effects and changes in plasma enzymes are estimated to occur at 15 μg/m3. The vaporized Hg eventually settles in soil and the sediment of lakes, rivers, bays, and oceans and is transformed by anaerobic organisms into methylmercury (MeHg). In bodies of water, the MeHg is absorbed by phytoplankton, which is ingested by zooplankton and fish, thereby contaminating the food chain. It especially accumulates in long-lived predatory species such as shark and swordfish (WHO 2007).
Elemental Hg and MeHg are toxic to the central and peripheral nervous system. The inhalation of Hg vapor can produce harmful effects on the nervous, digestive, and immune systems and the lungs and kidneys and may be fatal (WHO 2007). Children are especially vulnerable and may be exposed directly by eating MeHg-contaminated fish. MeHg bioaccumulates in fish and when consumed by pregnant women may lead to neurodevelopmental problems in the developing fetus. Transplacental exposure is the most dangerous because the fetal brain is very sensitive (WHO 2007). Neurological symptoms include mental retardation, seizures, vision and hearing loss, delayed development, language disorders, and memory loss. In children, acrodynia, a syndrome characterized by red and painful extremities, has been reported to result from chronic Hg exposure (WHO 2007, 2008).
Elemental Hg, the form of Hg used in gold amalgamation, is a liquid that volatilizes rapidly (WHO 2007). In humans, elemental Hg is typically measured in blood or urine (WHO 2003, 2008). MeHg, the form of Hg that contaminates fish, is typically measured in blood, cord blood, or hair. Sample collection of hair is the preferred method of biomonitoring for MeHg because it is less invasive than blood sampling. Blood Hg concentrations characterize recent or current exposure (WHO 2008). In populations where exposure to Hg occurs primarily through consumption of contaminated fish, most of the total Hg in the blood is organic and can be used as a measure of MeHg exposure (WHO 2008).
Given the prominence of ASGM as a significant source of global Hg and that national plans, as specified by the Minamata Convention, call for the collection of health data, this review was undertaken to identify studies that describe health effects and exposure in ASGM communities. We hoped that such information can serve as a resource to health authorities in those countries where ASGM is currently practiced.
To identify relevant studies, we searched PubMed (http://www.ncbi.nlm.nih.gov/pubmed/) as well as ScienceDirect (http://www.sciencedirect.com/) and Google Scholar (http://scholar.google.com/). The following search terms were included: Hg, MeHg, fish consumption, hair, blood, urine, neurological effects, kidney effects, health effects, and gold mining. The names of numerous countries where ASGM is known to occur were also included in searches. A total of 1,317 potentially relevant studies were identified. Studies were considered relevant if they identified health effects or measured hair or urinary Hg concentrations in individuals residing in an area affected by ASGM. We identified 72 studies that fit our criteria for relevance. We divided the studies into two categories: a) studies that identified health effects in ASGM communities (Table 1), and b) studies that reported hair or urine Hg in ASGM communities or communities affected by ASGM (see Supplemental Material, Tables S1, S2, and S4). Several studies included measurements of blood Hg as well as hair Hg (see Supplemental Material, Tables S2 and S3). We included studies published through December 2012.
We compared hair concentrations with 2.5 μg/g, the hair concentration associated with the provisional tolerable weekly intake (PTWI) [Bellanger et al. 2013; Food and Agricultural Organization of the United Nations (FAO)/WHO 2003]. The PTWI was established to protect the developing fetus from neurotoxic effects (WHO 2007). In 2006, the Joint FAO/WHO Expert Committee on Food Additives (JECFA) concluded that life stages other than the embryo and fetus may be less sensitive to the effects of MeHg. Available data did not allow the JECFA to make firm conclusions with respect to children ≤ 17 years of age and therefore stated that the PTWI also applied to children (WHO 2007).
In the present study, we compared urine concentrations with 50 μg Hg/g-creatinine, a concentration at which renal tubular effects and changes in plasma enzymes are expected to occur (WHO 2000). Urine concentrations were also compared with 100 μg Hg/g-creatinine, a urinary concentration at which the probability of developing the classical neurological signs of Hg intoxication is high (WHO 1991). For purposes of presentation, only studies that reported ranges and mean urinary or hair Hg were included in figures to demonstrate the extremes of Hg exposure. All study results, however, are presented in Supplemental Material, Tables S1–S4.
We identified 17 studies in the literature that described health effects in ASGM communities (Table 1). The health effects studies were conducted in 10 different countries on three continents (South America, Africa, and Asia). All of the studies were cross-sectional.
Numerous biomarker (hair, blood, urine) studies have been conducted in ASGM populations. The biomarker studies were conducted in 19 different countries on three continents. Studies that reported hair Hg concentrations among residents of ASGM communities, miners, and environmentally exposed populations are reported in Supplemental Material, Table S1. These studies were conducted in 14 different countries. Supplemental Material, Table S2, includes studies that examined hair and blood Hg in the same population; 8 different countries are represented by these studies. Supplemental Material, Tables S3 and S4 contain studies that reported Hg concentrations in blood and urine, respectively. The studies on blood and urinary Hg were conducted in 5 and 13 countries, respectively.
Figure 1 shows urinary Hg concentrations from studies where both a mean (horizontal blue line) and a range (vertical line) were reported. “Neurological symptoms” designates the 100 μg/g-creatinine value for neurological effects identified by WHO (1991). “Kidney effects” designates the 50 μg/g-creatinine concentration at which renal tubular effects are expected to occur (WHO 2000).
Figure 1 – Means (horizontal blue lines) and ranges (vertical lines) of urinary Hg found in ASGM populations. The red line indicating “Neurological symptoms” designates the 100 μg/g-creatinine value for neurological effects identified by WHO (1991). The black line indicating “Kidney effects” designates the 50 μg/g-creatinine concentration at which renal tubular effects are expected to occur (WHO 2000). For more information, see Supplemental Material, Table S4. References that appear on the x-axis more than once indicate that the study included more than one study group [e.g., merchants and miners in Harari et al. (2012)].
aThe highest value for data in this category was 1697.39 μ/g-creatinine. bThe lowest value for data in this study was < LOD; the highest value was 1697 μg/g-creatinine.
Figure 2 shows hair Hg concentrations in female residents of ASGM communities from studies where both a mean and a range (where shown) were reported. Most of the means and all of the maximum concentrations reported were above the PTWI. Figure 3 shows means and ranges of hair Hg of children and infants in ASGM communities. Women and children were selected for Figures 2 and 3, respectively, because the developing fetus and children are considered more vulnerable to the effects of MeHg.
Figure 2 – Means (horizontal blue lines) and ranges (vertical lines) of hair Hg of women in studies of residents of ASGM communities. PTWI, provisional tolerable weekly intake. For more information, see Supplemental Material, Table S1.
aThe lowest value for these studies was < LOD.
Figure 3 – Means (horizontal blue lines) and ranges (vertical lines) of hair Hg of children and infants in studies of residents of ASGM communities. PTWI, provisional tolerable weekly intake. For more information, see Supplemental Material, Table S2.
The most common health effect reported among workers engaged in ASGM are neurological effects (Table 1). These include tremor, ataxia, memory problems, and vision disorder and were found to occur not just among those engaged in mining activities but also among fish consumers living downstream of mining activities.
Increased urinary excretion of the enzyme N-acetyl-β-D-glucoaminidase (NAG), a biomarker of damage to the proximal tubules of the kidney, was found among occupationally exposed individuals (Drake et al. 2001) as well as among those living in a community where gold mining had been practiced (Tian et al. 2009). Kidney dysfunction was clinically diagnosed in 9 of 103 individuals in a gold mining population in Peru (Yard et al. 2012). Those reporting kidney dysfunction had higher urine total Hg concentrations [geometric mean (GM) = 12.0 μg/g-creatinine] than those not reporting kidney dysfunction (GM = 5.1 μg/g-creatinine; p < 0.05). See Table 1 for further information on kidney effects.
Four studies conducted in Brazil suggest that Hg exposure among gold miners and in gold mining communities is associated with an increase in the prevalence of markers of autoimmune dysfunction (Alves et al. 2006; Gardner et al. 2010; Nyland et al. 2011; Silva et al. 2004). See Table 1 for the details of each study.
Ten of the study populations in Table 1 were in South America, six were in Brazil alone. Only two of the study populations are in Africa; four are in Asia. The number of studies in a geographic region should not be construed to represent the magnitude of the problem in that region, however. The number of artisanal and small-scale gold miners and the amount of Hg released from ASGM is as great, if not greater, a problem in Asia and Africa as it is in South America (UNEP 2013c).
Harari et al. (2012), Steckling et al. (2011), Tomicic et al. (2011), Paruchuri et al. (2010), Bose-O’Reilly et al. (2008, 2010a), Counter et al. (2006), and Drake et al. (2001) all reported urinary Hg concentrations well above 100 μg Hg/g-creatinine. Data on urinary concentrations of Hg are provided in Figure 1 and Supplemental Material, Table S4. The WHO (1991) considers 100 μg Hg/g-creatinine to be the level above which the probability of developing classical neurological signs of Hg intoxication is high. High urinary Hg concentrations were particularly evident among those who amalgamate Hg or heat Hg to remove it from the amalgam. As an example of the elevated urinary concentrations found among small-scale gold mining operations, Tomicic et al. (2011) reported that the mean urinary Hg among gold dealers in Burkina Faso was 299.1 μg Hg/g-creatinine. Gold dealers were believed to have the most frequent exposure to Hg vapor. Drake et al. (2001) reported that among self-employed gold miners in Venezuela, the mean urinary Hg concentration was 148 μg Hg/g-creatinine; the high end of the range was 912 μg Hg/g-creatinine. Bose-O’Reilly et al. (2008) reported that the mean urinary Hg concentration among a sample of 80 children working with Hg was 36.50 μg Hg/g-creatinine; the high end of the range was 666.87 μg Hg/g-creatinine. The children who worked in small-scale gold mining operations in Indonesia and Zimbabwe ranged in age from 9 to 17 years. Umbangtalad et al. (2007) found that Thai schoolchildren living near, but not working in, small-scale gold mining operations had increased urinary Hg concentrations.
Hair Hg reflects the ingestion of Hg from fish (MeHg) (WHO 1990). The mean hair Hg concentration in virtually all of the 55 studies conducted in ASGM areas or areas affected by ASGM are above the concentration (2.5 μg/g) associated with the WHO’s PTWI (Figures 2 and 3; see also Supplemental Material, Tables S1 and S2). Many of the studies reported hair concentrations > 14 μg/g, which the FAO/WHO (2003) considers a no observed effects level (NOEL). The NOEL is based on neurotoxic effects in the fetus; the PTWI was established to protect the fetus from neurotoxic effects (WHO 2007). In 2006, the JECFA concluded that life stages other than the embryo and fetus may be less sensitive to the effects of MeHg. Because of a lack of data on children < 17 years of age, the JECFA concluded that the PTWI should also apply to children (WHO 2007). Hair Hg concentrations above those that reflect the PTWI and NOEL should, therefore, not be indicative of health effects in adults. The WHO (1990) concluded that a hair Hg concentration of 50 μg Hg/g would indicate a low (5%) risk of neurological damage to adults. Some of the studies listed in Table 1 [e.g., Harada et al. (2001) and Lebel et al. (1998)], however, suggest that neurological effects may be evident in adults at hair Hg concentrations of < 50 μg Hg/g. Blood concentrations of Hg may reflect exposure to either MeHg or inorganic Hg (WHO 1990, 2003). The background level of Hg in blood for those who do not eat fish is 2 μg Hg/L (WHO 2003).
Individuals involved in the gold mining operations, their families, and those in the gold mining communities are exposed to dangerous levels of elemental Hg vapor, as evidenced by urinary Hg concentrations. This evidence includes extremely elevated urinary Hg concentrations in children who work in the mines and children who live in the areas where small-scale gold mining occurs. Residents in the gold mining communities and downstream of the gold mining communities consume fish that may be heavily contaminated with MeHg, as demonstrated by hair Hg measurements. Current studies indicate that those in the ASGM communities experience neurological effects, kidney effects, and possibly immunotoxic/autoimmune effects from Hg exposure. Not only is the danger widespread globally, but the problem is expected to grow. National public health strategies on ASGM, as required by the Minamata Convention, should be implemented immediately.
Akagi H, Castillo ES, Cortes-Maramba N, Francisco-Rivera AT, Timbang TD. 2000. Health assessment for mercury exposure among schoolchildren residing near a gold processing and refining plant in Apokon, Tagum, Davao del Norte, Philippines. Sci Total Environ 259(1–3):31–43.
AMAP/UNEP (Arctic Monitoring and Assessment Programme/United Nations Environment Programme). 2013. Technical Background Report for the Global Mercury Assessment 2013. Available: http://www.amap.no/documents/download/1265 [accessed 3 June 2014].
Baeuml J, Bose-O’Reilly S, Matteucci Gothe R, Lettmeier B, Roider G, Drasch G, Siebert U. 2011. Human biomonitoring data from mercury exposed miners in six artisanal small-scale gold mining areas in Asia and Africa. Minerals 1(1):122–143.
Bellanger M, Pichery C, Aerts D, Berglund M, Castaño A, Cejchanová M, et al. 2013. Economic benefits of methylmercury exposure control in Europe: monetary value of neurotoxicity prevention. Environ Health 12(1):3; doi: 10.1186/1476-069X-12-3.
Cordier S, Garel M, Mandereau L, Morcel H, Doineau P, Gosme-Seguret S, et al. 2002. Neurodevelopmental investigations among methymercury-exposed children in French Guiana. Environ Res Section A 89:1–11.
Dórea JG, Souza JR, Marques RC, Isejima C. 2012. Neurodevelopment of Amazonian infants: antenatal and postnatal exposure to methyl- and ethylmercury. J Biomed Biotechnol 2012:132876; doi: 10.1155/2012/132876.
Drake PL, Rojas M, Reh CM, Mueller CA, Jenkins FM. 2001. Occupational exposure to airborne mercury during gold mining operations near El Callao, Venezuela. Int Arch Occup Environ Health 74(3):206–212.
Drasch G, Böse-O’Reilly S, Beinhoff C, Roider G, Maydl S. 2001. The Mt. Diwata study on the Philippines 1999—assessment mercury intoxication of the population by small scale gold mining. Sci Total Environ 267(1–3):151–168.
FAO/WHO (Food and Agricultural Organization of the United Nations/World Health Organization). 2003. Summary and Conclusions, Expert Committee on Food Additives. 61st Meeting. Rome, 10–19 June 2003. Available: http://www.who.int/foodsafety/chem/jecfa/summaries/en/summary_61.pdf [accessed 20 May 2013].
Gardner RM, Nyland JF, Silva IA, Ventura AM, Souza JM, Silbergeld EK. 2010. Mercury exposure, serum antinuclear/antinucleolar antibodies, and serum cytokine levels in mining populations in Amazonian Brazil: a cross-sectional study. Environ Res 110(4):345–354.
Harada M, Nakanishi J, Yasoda E, Pinheiro MC, Oikawa T, de Assis Guimarães G, et al. 2001. Mercury pollution in the Tapajos River basin, Amazon: mercury level of head hair and health effects. Environ Int 27(4):285–290.
Kwaansa-Ansah EE, Basu N, Nriagu JO. 2010. Environmental and occupational exposures to mercury among indigenous people in Dunkwa-On-Offin, a small scale gold mining area in the South-West of Ghana. Bull Environ Contam Toxicol 85(5):476–480.
Malm O, Dórea JG, Barbosa AC, Pinto FN, Weihe P. 2010. Sequential hair mercury in mothers and children from a traditional riverine population of the Rio Tapajós, Amazonia: seasonal changes. Environ Res 110(7):705–709.
Nyland JF, Fillion M, Barbosa F Jr, Shirley DL, Chine C, Lemire M, et al. 2011. Biomarkers of methylmercury exposure immunotoxicity among fish consumers in Amazonian Brazil. Environ Health Perspect 119:1733–1738; doi: 10.1289/ehp.1103741.
Paruchuri Y, Siuniak A, Johnson N, Levin E, Mitchell K, Goodrich JM, et al. 2010. Occupational and environmental mercury exposure among small-scale gold miners in the Talensi–Nabdam District of Ghana’s Upper East region. Sci Total Environ 408(24):6079–6085.
Pinheiro MC, Müller RC, Sarkis JE, Vieira JL, Oikawa T, Gomes MS, et al. 2005. Mercury and selenium concentrations in hair samples of women in fertile age from Amazon riverside communities. Sci Total Environ 349(1–3):284–288.
Silva IA, Nyland JF, Gorman A, Perisse A, Ventura AM, Santos EC, et al. 2004. Mercury exposure, malaria, and serum antinuclear/antinucleolar antibodies in Amazon populations in Brazil: a cross-sectional study. Environ Health 3(1):11; doi: 10.1186/1476-069X-3-11.
Steckling N, Bose-O’Reilly S, Gradel C, Gutschmidt K, Shinee E, Altangerel E, et al. 2011. Mercury exposure in female artisanal small-scale gold miners (ASGM) in Mongolia: an analysis of human biomonitoring (HBM) data from 2008. Sci Total Environ 409(5):994–1000.
Tian L, Guo HF, Gao A, Lu XT, Li QY. 2009. Effects of mercury released from gold extraction by amalgamation on renal function and environment in Shanxi, China. Bull Environ Contam Toxicol 83(1):71–74.
Umbangtalad S, Parkpian P, Visvanathan C, Delane RD, Jugsujinda A. 2007. Assessment of Hg contamination and exposure to miners and schoolchildren at a small-scale gold mining and recovery operation in Thailand. J Environ Sci Health A Tox Hazard Subst Environ Eng 42(14):2071–2079.
UNEP (United Nations Environment Programme). 2008. Module 3: Mercury Use in Artisanal and Small Scale Gold Mining. Available: http://www.unep.org/hazardoussubstances/Portals/9/Mercury/AwarenessPack/English/UNEP_Mod3_UK_Web.pdf [accessed 19 July 2013].
UNEP (United Nations Environment Programme). 2012. Reducing Mercury Use in Artisanal and Small-Scale Gold Mining: A Practical Guide. Available: http://www.unep.org/hazardoussubstances/Portals/9/Mercury/Documents/ASGM/Techdoc/UNEP%20Tech%20Doc%20APRIL%202012_120608b_web.pdf [accessed 18 December 2012].
UNEP (United Nations Environment Programme). 2013a. Global Mercury Assessment 2013—Sources, Emissions, Releases and Environmental Transport. Available: http://www.unep.org/PDF/PressReleases/GlobalMercuryAssessment2013.pdf [accessed 3 June 2014].
UNEP (United Nations Environment Programme). 2013b. Mercury, Negotiations: The Negotiating Process. Available: http://www.unep.org/hazardoussubstances/Mercury/Negotiations/tabid/3320/Default.aspx [accessed 1 November 2013].
UNEP (United Nations Environment Programme). 2013c. Mercury—Time to Act. Available: http://www.unep.org/PDF/PressReleases/Mercury_TimeToAct.pdf [accessed 3 June 2014].
WHO (World Health Organization). 1990. Methylmercury. Environmental Health Criteria 101. Geneva:WHO. Available: http://www.inchem.org/documents/ehc/ehc/ehc101.htm [accessed 20 May 2013].
WHO (World Health Organization). 1991. Inorganic mercury. Environmental Health Criteria 118. Geneva:WHO. Available: http://www.inchem.org/documents/ehc/ehc/ehc118.htm [accessed 20 May 2013].
WHO (World Health Organization). 2000. Air Quality Guidelines for Europe. 2nd ed. Copenhagen:WHO. Available: http://www.euro.who.int/__data/assets/pdf_file/0005/74732/E71922.pdf [accessed 15 October 2013].
WHO (World Health Organization). 2003. Elemental Mercury and Inorganic Mercury Compounds: Human Health Aspects. Concise International Chemical Assessment Document 50. Geneva:WHO. Available: http://www.who.int/ipcs/publications/cicad/en/cicad50.pdf [accessed 15 October 2013].
WHO (World Health Organization). 2007. Exposure to Mercury: A Major Public Health Concern. Geneva:WHO Available: http://www.who.int/ipcs/features/mercury.pdf [accessed 15 October 2013].
WHO (World Health Organization). 2008. Mercury: Assessing the Burden of Disease at National and Local Levels. Environmental Burden of Disease Series, No. 16. Geneva:WHO. Available: http://whqlibdoc.who.int/publications/2008/9789241596572_eng.pdf [accessed 15 October 2013].
Upcoming Recruitment: Editor-in-Chief for Environmental Health Perspectives
The National Institute of Environmental Health Sciences (NIEHS) will soon commence searching for the next Editor-in-Chief of Environmental Health Perspectives. For more information visit our Careers and Funding page.
CEHN February 2015 Article of the Month
“Preconception Maternal and Paternal Exposure to Persistent Organic Pollutants and Birth Size: The LIFE Study” (Environ Health Perspect; DOI:10.1289/ehp.1308016) has been selected by the Children’s Environmental Health Network (CEHN) as its February 2015 Article of the Month. These CEHN summaries discuss the potential policy implications of current children’s environmental health research.
Sign Up to Receive E-mail Alerts
Recent Advance Publications
Combining PM2.5 Component Data from Multiple Sources: Data Consistency and Characteristics Relevant to Epidemiological Analyses of Predicted Long-Term Exposures
In Utero and Childhood Polybrominated Diphenyl Ether Exposures and Body Mass at Age 7 Years: The CHAMACOS Study
Blood Pressure, Left Ventricular Geometry, and Systolic Function in Children Exposed to Inorganic Arsenic
Rapid Responses and Mechanism of Action for Low-Dose Bisphenol S on ex Vivo Rat Hearts and Isolated Myocytes: Evidence of Female-Specific Proarrhythmic Effects
Natural Cause Mortality and Long-Term Exposure to Particle Components: An Analysis of 19 European Cohorts within the Multi-Center ESCAPE Project