Lead exposure from soil in Peruvian mining towns: a national assessment supported by two contrasting examples
Alexander van Geen a, Carolina Bravo b, Vladimir Gil c, Shaky Sherpa d & Darby Jack b
a. Lamont-Doherty Earth Observatory of Columbia University, Route 9W, Palisades, New York, NY, 10964, United States of America (USA).
b. Mailman School of Public Health, Columbia University, New York, USA.
c. Center for Environmental Research and Conservation, Columbia University, New York, USA.
d. Center for International Earth Science Information Network, Columbia University, Palisades, USA.
Correspondence to Alexander van Geen (e-mail: firstname.lastname@example.org).
(Submitted: 18 April 2012 – Revised version received: 28 August 2012 – Accepted: 30 August 2012 – Published online: 10 October 2012.)
Bulletin of the World Health Organization 2012;90:878-886. doi: 10.2471/BLT.12.106419
Children and adults are still routinely exposed to very high levels of lead in developing countries, particularly in regions with a long mining history, such as the Andes.1-4 This study focuses on Peru, which ranks among the world’s top five producers of silver, zinc, lead and copper5 and has a long and conflict-ridden mining history.6 Exposure to lead in this country may have been prolonged, despite some widely publicized and severe cases,7 by the importance of the revenue generated by the mining industry, weak regulation, a lack of information about contamination and a perception that the cost of interventions might be prohibitive. The premise of this study is that many, perhaps most, egregious cases of mining-related childhood lead exposure in Peru, and similarly affected countries in South America and Africa, could be avoided at a relatively modest cost by systematically mapping hot spots for lead in soil in mining towns where ore is currently processed or has been processed in the past. Interventions carried out around mines, ore processing plants and smelters in other parts of the world have already been shown to reduce dramatically childhood exposure to lead.8-11
The exploitation of metal-rich deposits in the Andes dates from pre-colonial times.12 Then, the focus was on silver, as it was during the Spanish colonial era. The extensive use of mercury to extract silver through the process of amalgamation undoubtedly had a substantial, albeit localized, impact on the health of workers.13,14 Potentially just as important, however, especially when their cumulative effect is considered, could be the health impact of the mine tailings left over once the most concentrated ore has been separated. These tailing are enriched in lead and were generated over centuries of mining silver, copper, zinc and lead deposits throughout the region. Today when a new mine enters into operation, the mining company attempts to minimize the risk of exposure by purchasing surrounding tracts of land. In the past, however, population centres typically became established near a mine and dwellings were built on top of mine tailings.15 In such places, even today it is still common for children to ingest large quantities of lead by playing in contaminated soil or ingesting lead-laden dust at home.10,16-19 Currently, Peru has no standard for the lead content of soil.
The assumption underlying this study is that lead contamination of soil is heterogeneously distributed and, consequently, the level of contamination within a few kilometres of one mining-related operation can differ greatly from that close to another. If suitable maps were made available locally, young children, who are especially at risk of ingesting soil when playing, could be induced to avoid the most contaminated areas.20 Our aim was to evaluate the potential benefits of such an intervention on a national scale by carrying out a spatial analysis of mining operations in Peru in relation to population density. To the best of our knowledge, no similar study has previously been carried out. In addition, we performed surveys of the local distribution of lead in soil at two locations to illustrate low- and high-risk scenarios. The study focused on lead contamination linked to the exploitation of deposits of polymetallic ore, including gold-containing ore, and therefore excluded contamination associated with cement production and other extractive activities, which could also have a substantial effect on health.
We obtained the geographical coordinates of 7997 sites involved in four types of activity associated with mining: (i) 113 industrial-scale mines in operation in 2009; (ii) 138 ore processing plants; (iii) 3 smelters; and (iv) 7743 “legacies” of past mining activities. Since none of the existing data compilations was exhaustive, the information was drawn from several sources (Appendix A, available at: http://www.ldeo.columbia.edu/~avangeen/mining). The analysis does not include undocumented artisanal mines or informal and unreported mining-related activities, which can also be major sources of lead exposure.11
Details of the 7997 sites, including their attributes, were entered into a spreadsheet (Appendix B, available at: http://www.ldeo.columbia.edu/~avangeen/mining) and the data were mapped using ArcGIS software (esri, Redlands, United States of America) and the geographical coordinate system GCS WGS 1984. A circle with a radius of 5 km, termed a “buffer”, was created around each site; if there was an overlap, circles were merged. The 5-km radius is a compromise. In some cases, the population exposed to lead may have been overestimated because contamination did not extend as far as 5 km from the mining-related operation. In others, the population may have been underestimated because sites that are active at present or were active in the past were not reported. Data on individual sites and merged buffers were converted into computer files with a .kmz extension (Appendix C, available at: http://www.ldeo.columbia.edu/~avangeen/mining) so they could be viewed on Google Earth (Google Inc., Menlo Park, USA).
Data on the estimated size of the population of Peru in 2000 were obtained from the Global Rural–Urban Mapping Project version 1 (GRUMPv1) data product, available at a resolution of 30 arc-seconds, or ~1 km at the equator from CIESIN (Center for International Earth Science Information Network, Palisades, USA).21 The data were imported into ArcGIS in a grid format. In addition, an overlay of GRUMPv1 population data for Peru was created in a .kmz file format (Appendix C) for comparison with the location of the mining operations in Google Earth. The size of the population living within each 5-km-radius buffer was estimated using the zonal overlay method in ArcGIS: by defining the 5-km buffers as zones, the population exposed within each buffer was calculated using the raster grid population count.
Local soil lead surveys
Two contrasting locations were selected to document the spatial variability of lead contamination of surface soil: the historic mining town of Cerro de Pasco, which is situated 4400 m above sea level in the Andes and has a population of 70 000, and the more recent mine and ore processing plant near Huaral, situated 150 m above sea level only a few kilometres from the Pacific Ocean, with a population of 160 000.
Lake sediment records indicate that heavy metals from the mining and smelting of silver-bearing ores in Cerro de Pasco were being released into the atmosphere as early as 1400 years ago.12,14 In the 1800s, deposition of lead and mercury from smelting increased dramatically with the growth of the Ciudad Real de Minas, as the town was also known. Deposition peaked in the 1950s after the copper and zinc mines were purchased by the United States Cerro de Pasco Investment Co. Subsequently, the mines were nationalized and exploited by the Centromin conglomerate until, in 1999, the Peruvian Compañía Minera Volcan bought the main mines in Cerro de Pasco and the associated Paragsha ore processing plant. The town of Cerro de Pasco has been built around an open-pit mine and on top of mine tailings. In recent decades, vast quantities of waste rock and tailings have been accumulating over an area of approximately 10 km2, several kilometres to the south-west of the main pit and further away from the main population centre.22
The María Teresa polymetallic (i.e. zinc, lead and silver) mine and associated Minera Colquisiri SA ore processing plant started operating 7 km west of the town of Huaral in 1984. Human activity around the perimeter of the mine is primarily agricultural, mostly fruit trees and hog farms. However, a few hamlets were also built close to the perimeter of the site. In contrast to Cerro de Pasco, there is no large population centre close to the mine and tailings are stored in a pond located within the plant property.
In May 2009, the distribution of lead in surface soil in the town of Cerro de Pasco and in areas outside the fence surrounding the María Teresa mine and ore processing plant near Huaral were mapped using a hand-held X-ray fluorescence analyser (Innov-X Alpha, Olympus Corporation, Tokyo, Japan), as used in other studies.11 The precision of the measurements estimated by the manufacturer’s software typically ranged from 17 to 250 mg/kg for soil containing 400 to 11 000 mg/kg lead, respectively. The accuracy of the analyzer was evaluated over a period of 10 days using three soil standards from the United States National Institute of Standards and Technology: Standard Reference Material (SRM) 2710 with a mean concentration of lead in soil of 5532 mg/kg (standard deviation, SD: 80), SRM 2711 with 1162 mg/kg (SD: 31) and SRM 2709 with 18.9 mg/kg (SD: 0.5). These measurements averaged 96 % (SD: 4; 11 measurements), 97 % (SD: 7; 7 measurements) and 89% (SD: 10; 4 measurements) of the certified values for the three soil standards, respectively. A .kmz file was created to enable the soil lead data to be viewed on Google Earth (Appendix C).
In the spatial analysis, a total of 312 nonoverlapping buffers were obtained by combining the 5-km-radius circles around the 254 active mining operations (i.e. mines, ore processing plants and smelters) with those around the 7743 mining legacies. The average size of these buffers was 170 km2, with the largest covering an area of 1800 km2. Of the 312 buffers, 227 did not contain a single active mine, ore processing plant or smelter but did include a total of 3030 legacy sites. Another 52 buffers contained a combination of legacies and active mining operations, whereas the remaining 33 buffers contained only active mines, ore processing plants or smelters.
In 2000, the population of Peru was approximately 30 million and was distributed across 195 coastal, mountain (Andean) and tropical forest (Amazonian) provinces. Around 90% of sites with active mining operations or mining legacies were located in mountain provinces, with the remaining sites divided roughly equally between coastal and tropical forest provinces (Fig. 1). The average population density of Peru was only 21 people per square kilometre and about two thirds of the buffers were located within areas with a population density below the national average. In total, 1.6 million people resided within 5 km of an active mine, ore processing plant or smelter or a mining legacy.
Fig.1. The 312 sitesa with active mining operations or mining legacies associated with lead in soil, Peru, 2009.
The size of the population residing in the different buffers ranged widely. It was less than 1000 in each of the 148 buffers with the smallest populations. In another 135 buffers, the population ranged from 1000 to 10 000. However, the remaining 29 buffers (Table 1) accounted for more than two thirds of the total population living within 5 km of an active mining operation or mining legacy: the population in each of these buffers ranged from 10 000 to 129 000. The population density averaged 175 people per square kilometre in these 29 buffers and was below the national average in only 2 of the 29. Eleven of these buffers contained only mining legacies. Together, the 29 buffers encompassed a total of 3438 legacies, 52 active mines, 58 ore processing plants and 2 smelters.
The buffer centred around Cerro de Pasco ranked second in our national assessment: it covered the second largest area, at 1659 km2, and had the second largest population, at 119 178 inhabitants (Table 1). The largest buffer had a slightly larger population, contained 52 legacies and no active mining operations and included Huancayo, Peru’s fifth largest city. The Cerro de Pasco buffer contained 12 active mines, 9 ore processing plants and 349 legacies. Our soil survey centred on the main open-pit mine, which continues to be exploited on a massive scale and covers 5 km2 of the buffer. Only 35 of the 74 soil samples (47%) had a lead concentration below the maximum of 1200 mg/kg recommended by the United States Environmental Protection Agency for soil in residential areas where children do not play.23 Soil lead concentrations above 1200 mg/kg were measured all around the open pit but no further than 1 km from its edge (Fig. 2). The five highest concentrations, which ranged between 5000 and 12 000 mg/kg, were all observed in samples taken from within 500 m of the western margin of the pit. Only 11 of the 74 soil samples (15%) had lead concentrations below the threshold of 400 mg/kg recommended by the Environmental Protection Agency for soil in residential areas where children play. Soil lead concentrations below 400 mg/kg were found primarily in the outer northern and eastern sections of the town.
Fig. 2. Aerial image of the main open-pit mine and surrounding town of Cerro de Pasco, Peru, showing locations where the lead concentration in soil a was measured, 2009.
The second location selected for our soil lead survey was in a buffer that ranked fifteenth by population in our assessment and contained only one mine, one ore processing plant and four legacies (Fig. 3). However, the buffer was 90 km2 in area and extended to the outskirts of the town of Huaral. Consequently, it encompassed a sizeable population of 21 705 (Table 1). The soil measurements obtained from this site contrasted markedly with those from Cerro de Pasco. Only 4 of the 47 samples (8.5%) had a lead concentration above 1200 mg/kg and the maximum was 2300 mg/kg. The high lead concentrations were all observed along a road and in cultivated fields within 200 m of the perimeter of the plant. The lead concentration in soil at most other locations within that distance was less than 400 mg/kg.
Fig. 3. Aerial image of the mine and ore processing plant near Huaral, Peru, showing locations where the lead concentration in soil a was measured, 2009.
A study conducted in 2007 by the United States Centers for Disease Control and Prevention in collaboration with the Peruvian authorities showed that the lead content of blood drawn from 52% of 163 children living in Cerro de Pasco exceeded the intervention threshold of 10 μg/dL.24 In the Ayapoto area, west of the mine pit where soil was highly contaminated (Fig. 2), the blood lead content exceeded 10 μg/dL in 88% of local children and concentrations as high as 62 μg/dL were measured. In contrast, blood lead levels exceeded 10 μg/dL in only 9.4% of 194 women of child-bearing age from the same areas of the town.
The 2007 study also reported 32 soil lead measurements for Cerro de Pasco in the 150 to 20 000 mg/kg range, with the highest values again being consistently observed in Ayapoto.24 The geographical association between the high blood lead content in children and the high soil lead content, and the absence of a similar association in women of child-bearing age, suggests that the primary pathway of lead exposure in children in Cerro de Pasco is the ingestion of soil and soil dust. The association between childhood exposure and soil contamination observed in Cerro de Pasco is consistent with that seen in studies of the effect of lead mining, ore processing, and smelting carried out elsewhere, including other parts of Latin America.10,17,19,25-26
We are not aware of any studies of the blood lead level in the population living near the Colquisiri mine in our second selected location. However, given the relatively low soil lead levels we observed (Fig. 3), it seems reasonable to assume that the population residing in Huaral was much less exposed than that in Cerro de Pasco.
Although Peru phased out leaded gasoline in 2004, occasional exposure from leaded paint cannot be excluded.16 In addition, exposure from the local manufacturing and recycling of batteries or the use of a lead glaze on tableware, both of which have been shown to be substantial in other developing countries, is also possible.27-29
Two long-term studies of lead in children’s blood carried out in Australia and the United States, respectively, are particularly relevant to the situation in Cerro de Pasco. In the lead mining town of Broken Hill, Australia, the blood lead content of all school-aged children was greater than 40 μg/dL in 1982.19 Between 1991 and 2003, as a result of various interventions, the number of children with a concentration above 10 μg/dL declined from 85 to 32%. Lead isotope analysis showed that soil and dust that was contaminated to a level of 1000 to 7000 mg/kg, either by natural erosion of the ore or mining, was a major source of lead in children’s blood, although occasionally leaded gasoline and lead-based paint also made a substantial contribution.16
Around the lead mine and smelter at Bunker Hill, Idaho, United States, the mean blood lead level in children was 70 μg/dL in the early 1970s. At the time the smelter was operating without any emission controls, the concentration in yard soil averaged 7000 mg/kg and the house dust lead concentration was 12 000 mg/kg.18 Again as a result of a series of interventions, exposure declined dramatically: the proportion of children with a blood lead level greater than 10 μg/dL decreased from 45% in 1988 to 3% in 2001. In addition, the observation that children were still exposed after the smelter was closed, via the ingestion of soil and house dust, prompted the removal and replacement of house yard soil with a lead concentration greater than 1000 mg/kg. The remarkable reduction in the level of lead in children’s blood that was achieved in Bunker Hill sets an attainable target that can be applied to mitigation elsewhere, including areas as badly contaminated as Cerro de Pasco.
The levels of soil lead contamination around Cerro de Pasco and Huaral correspond to high- and low-risk scenarios for Peru, respectively, and therefore probably encompass the range of conditions in the other buffers. The effect of mining on the local population appears to be influenced primarily by its scale and duration. Mining started much earlier in Cerro de Pasco than in Huaral14 and led to the accumulation of a large amount of tailings on top of which the town was built. Moreover, the Cerro de Pasco buffer included 349 legacies compared with 4 in the Huaral buffer (Table 1). It is possible, then, that the number of legacies could provide a useful indication of the severity of lead contamination in locations where no soil measurements are available. Although 14 of the 29 largest buffers by population included active mining operations as well as at least one legacy, judging the severity of contamination on the basis of legacies alone could be misleading. For instance, the buffer that includes the infamous Doe Run smelter in Yauli Province, where extensive childhood lead exposure has been documented,7 does not include a single legacy.
The soil lead survey in Cerro de Pasco shows that contamination is far from uniform even under a high-risk scenario. Heterogeneous distributions of lead contamination, over and above the reduction associated simply with the distance from a mine or smelter, have been reported elsewhere. Consequently, given the magnitude of the effort and resources required to mitigate contamination,5,9 it is essential to identify those areas within a contaminated zone where soil replacement, or even relocation of the local population, is most needed.10 Soil assessments could be used to inform local government and families about the relative safety of various areas. These assessments, combined with information about the consequences of children ingesting lead-contaminated soil, could lead to a decrease in child exposure in the short term and enable the local community to participate in risk reduction.30
Unfortunately, currently there is no viable low-cost equipment that could reliably replace either X-ray fluorescence analysers or more laborious laboratory techniques.31 Public investment in risk mapping is, therefore, urgently needed. With the exception of one recent example in Nigeria,11 the use of costly large-scale soil removal or resettlement of communities to reduce mining-related lead exposure has been limited to high-income countries.18-19
In conclusion, our assessment that 1.6 million people in Peru could be exposed to lead in soil indicates that political will and resources are urgently needed to reduce the effect of exposure on the cognitive development of future generations. Our two case studies highlight the potential of local surveys of lead in soil to reduce exposure at a cost that is negligible relative to the revenues generated by mining, even in highly contaminated areas such as Cerro de Pasco. The key is to provide households and local government with appropriate information. In addition, systematic soil surveys could help identify areas where public health education and interventions are most needed. These approaches could also be beneficial in other countries with a legacy of mining lead-rich deposits. The dramatic reduction in emissions achieved by the owners of the large smelter complex of Ilo in southern Peru in response to emissions monitoring32 illustrates how interventions that rely on public data could be made more effective.
We thank government and industry representatives in Peru, Colin Cook, Sheila Xiah Kragie and Eduardo Ureta. Vladimir Gil is also a faculty member and researcher at the Graduate Environmental Development Program and the Department of Social Sciences at the Pontificia Universidad Católica del Perú, Lima, Peru, and is the general coordinator of the Consortium for the Study of the Economic Impact of Climate Change in Peru.
The study was funded by a grant from Cross-Cutting Initiatives, the Earth Institute at Columbia University (http://www.earthinstitute.columbia.edu). This is Lamont–Doherty Earth Observatory contribution number 7607.
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