Permitted water pollution discharges and population cancer and non-cancer mortality: toxicity weights and upstream discharge effects in US rural-urban areas
© Hendryx et al; licensee BioMed Central Ltd. 2012
Received: 23 February 2012
Accepted: 2 April 2012
Published: 2 April 2012
The study conducts statistical and spatial analyses to investigate amounts and types of permitted surface water pollution discharges in relation to population mortality rates for cancer and non-cancer causes nationwide and by urban-rural setting. Data from the Environmental Protection Agency's (EPA) Discharge Monitoring Report (DMR) were used to measure the location, type, and quantity of a selected set of 38 discharge chemicals for 10,395 facilities across the contiguous US. Exposures were refined by weighting amounts of chemical discharges by their estimated toxicity to human health, and by estimating the discharges that occur not only in a local county, but area-weighted discharges occurring upstream in the same watershed. Centers for Disease Control and Prevention (CDC) mortality files were used to measure age-adjusted population mortality rates for cancer, kidney disease, and total non-cancer causes. Analysis included multiple linear regressions to adjust for population health risk covariates. Spatial analyses were conducted by applying geographically weighted regression to examine the geographic relationships between releases and mortality.
Greater non-carcinogenic chemical discharge quantities were associated with significantly higher non-cancer mortality rates, regardless of toxicity weighting or upstream discharge weighting. Cancer mortality was higher in association with carcinogenic discharges only after applying toxicity weights. Kidney disease mortality was related to higher non-carcinogenic discharges only when both applying toxicity weights and including upstream discharges. Effects for kidney mortality and total non-cancer mortality were stronger in rural areas than urban areas. Spatial results show correlations between non-carcinogenic discharges and cancer mortality for much of the contiguous United States, suggesting that chemicals not currently recognized as carcinogens may contribute to cancer mortality risk. The geographically weighted regression results suggest spatial variability in effects, and also indicate that some rural communities may be impacted by upstream urban discharges.
There is evidence that permitted surface water chemical discharges are related to population mortality. Toxicity weights and upstream discharges are important for understanding some mortality effects. Chemicals not currently recognized as carcinogens may nevertheless play a role in contributing to cancer mortality risk. Spatial models allow for the examination of geographic variability not captured through the regression models.
A variety of water quality issues potentially impact rural and urban populations. Previous research identified 82,498 EPA-permitted water point pollution discharge sources in the US, of which 41% were located in rural areas of the country . Discharge of pollutants into surface water also has potential downstream impacts that may cross between urban and rural settings [2, 3]. Drinking water containing carcinogens such as arsenic or cadmium has been linked to various cancers and other diseases [4, 5].
There are many industrial water pollutants that may potentially impact human health. Exposure routes include both inhalation and ingestion of drinking water. Contaminated ground water in areas with hazardous waste sites has been shown to correlate with higher population cancer mortality rates and other human disease rates [6, 7]. Epidemiological research to investigate whether and how health may be influenced by industrial water pollutants is limited [4, 8], and research on the population health risks from the permitted surface water pollution discharge database represented in this study has apparently not been undertaken. Surface and ground water are interrelated and surface pollution can impair ground water .
In this study, we test the hypothesis that greater amounts of permitted toxic chemical pollutants in surface water will be associated with poorer population health. We are also interested in testing whether there is evidence for pollution discharges affecting population health downstream from its source, and whether these associations may be present differently between rural and urban environments. This is an exploratory study intended to establish whether associations exist between discharges and health outcomes; if such evidence is found, more specific hypotheses may be generated regarding relationships between specific chemicals and outcomes that may vary by geographic location as suggestions to encourage future research.
Results and discussion
Descriptive statistics of study variables
Total age-adjusted mortality rate per 100,000 for non-
Age-adjusted all-cancer mortality rate per 100,000
Age-adjusted kidney disease mortality rate per 100,000
Log of non-weighted, onsite non-carcinogenic discharges
Log of non-weighted, onsite carcinogenic discharges
Log of toxicity-weighted, onsite non-carcinogenic
Log of toxicity-weighted, onsite carcinogenic discharges
Log of toxicity-weighted, local and upstream non-
Log of toxicity-weighted, local and upstream carcinogenic
Percent adults aged 25+ with college or more education
Adult smoking rate
Adult obesity rate
Primary care physicians per 1,000 population
Percent African American
Percent Native American
Percent Asian American
Percent other non-White race
Percent metropolitan county
Percent non-metropolitan, adjacent county
Percent non-metropolitan, non-adjacent
Multiple regression coefficients, standard errors (SE), and p-values, age-adjusted mortality rates and four discharge specifications
Set 1: Log of onsite discharges not toxicity weighted
Set 2: Log of onsite discharges toxicity weighted
Set 3: Log of area weighted upstream discharges, toxicity weighted
Set 4: Log of area weighted upstream discharges, toxicity weighted, cross-validation
Kidney disease mortality
Total non-cancer mortality
Table 2 also shows the results of the cross-validation analyses as Set 4. In this analysis, area weighted and toxicity weighted discharges constitute the primary independent variable of interest. For cancer mortality, we observed an unexpected finding, namely, that non-carcinogen discharges were related to higher mortality at a more stringent p value than carcinogen discharges. For kidney disease the effect was stronger for non-carcinogen discharges as expected, but p values were significant for both discharge types. For total non-cancer mortality, only non-carcinogen discharges were related to a higher mortality rate.
Multiple regression coefficients, standard errors (SE), and p-values.
Adjacent non- metropolitan
Non-adjacent non- metropolitan
Kidney disease mortality
Total non-cancer mortality
Multiple regression results including covariates, for age-adjusted mortality rates and area-weighted and toxicity weighted discharges
Kidney disease mortality2
Total non- cancer mortality3
Log of non-carcinogen area weighted and toxicity weighted discharges
Log of carcinogen area weighted and toxicity weighted discharges
Percent adults with college education
Adult smoking rate
Adult obesity rate
Per capita primary care doctors
Percent African American
Percent Native American
Percent Asian American
Percent other race
Adjacent, non- metropolitan county
A test for spatial autocorrelation of the residuals from the ordinary least squares regression shows that there is significant autocorrelation among the residuals (Moran's I = 0.107, p < 0.001, inverse distance spatial weights matrix). The significance of this test suggests that either this model is missing one or more useful covariates or a spatial approach such as geographically weighted regression (GWR) may be appropriate . GWR is described more fully in the methods section.
Figure 4 reveals two broad areas that do not conform to the national trend of non-carcinogens having a stronger relationship with cancer mortality than carcinogens. These regions, highlighted in red, are in the intermountain west and in parts of the Midwest extending to a few places along the Atlantic Coast. Figure 5 does not show a clear trend in on-site versus the area-weighted sum of upstream releases, although three areas, the Mississippi River, Florida, and an area largely east of the Appalachian Mountains extending from New York City to South Carolina, show stronger on-site release effects. For most of the United States, unsurprisingly, the toxicity-weighted measures have a stronger relationship with cancer mortality, as shown in Figure 6. However, there are some regions in the Mid-Atlantic and southern areas of the country, colored blue, where the toxicity weights do not provide a stronger relationship.
GWR analyses comparing the area-weighted non-carcinogen releases with total mortality were also conducted, but are not shown in detail to conserve space. Further information is available from the authors. The local R2 values are higher than those for cancer mortality shown in Figure 3, ranging from 0.09 to 0.79, although the spatial pattern remains similar, with the highest values along the Pacific and Atlantic coasts. This greater R2 value is due to the improved correlation between the covariates and the mortality rate, as the local coefficient for the pollution variable is non-significant for most of the country. Only a small area in the Great Plains and Midwest spanning from western South Dakota through Nebraska and Iowa has a significantly positive coefficient and a significantly negative coefficient is only located in the same area of West Texas that has a significantly negative coefficient in Figure 2.
The results of the non-spatial analyses suggest that permitted discharges of chemical pollutants into surface waters are related to higher adjusted population mortality rates. More specifically, total non-cancer mortality is related to greater discharge quantities of chemicals classified as non-carcinogenic without need for toxicity weights or upstream discharges. For cancer mortality, the toxicity weights are necessary to detect associations between carcinogenic discharges and death rates, and for kidney disease mortality, both toxicity weights and area-weighted upstream discharges are necessary to detect discharge-mortality associations.
The cross-validation results suggest that chemicals not currently recognized as carcinogens may nevertheless play a role in contributing to cancer mortality risk. The potential carcinogenic properties of many chemicals are unknown and may be underestimated. Cross-validated results for kidney disease were significant but at a weaker level than for the non-cross-validation. There was a significant correlation between higher carcinogen releases and higher non-carcinogen releases (r = .69), so the cross-validation analysis of kidney disease may still be picking up non-carcinogen discharges. Some carcinogens such as cadmium or thallium are also recognized as causes of kidney damage . In contrast, the relatively small subset of known or suspected carcinogens was related to higher cancer mortality but not higher non-cancer mortality.
Kidney and total non-cancer death rates are most strongly related to discharges in rural areas not adjacent to metropolitan areas as compared to other urban-rural settings. It is possible that downstream effects from urban to rural areas may be a contributing factor, or downstream effects from one rural area to another.
The spatial analyses illustrate the wide variation of the local R2 values across the contiguous United States, as well as the variation in which model has the most explanatory power. The effects of both the chemical discharges and the covariates are not constant from one region of the country to another. Spatial models generally support the non-spatial analysis in that the releases of non-carcinogens are a better fit for the cancer mortality for most of the country (2303 out of 3109 counties) than the releases of carcinogens. For many of these counties, the improvement over not including any release variable is slight, indicating that the relative influence of chemical surface water discharges is small compared to effects of our covariates such as poverty or smoking rates. In many of the regions for which the improvement in local R2 was greatest, that improvement comes from the area weighted sum of all upstream releases of non-carcinogens, adjusted for toxicity. This suggests that for some, but not all, parts of the country, upstream releases may be an important factor.
A number of hypotheses may be suggested for future research based on the findings. First, studies may undertake whether chemicals currently not recognized as carcinogens may have carcinogenic properties. The number of chemicals with established carcinogenic information, whether that information is confirmatory or not, is small relative to the number of chemicals that are manufactured or used  There are many chemicals used in industrial processes or that are present in drinking water for which we have no information on health risks. The results of the current study can serve to encourage future research on understanding the possible health impacts for chemicals for which there is currently limited or no information. The choice of which chemicals to investigate may be guided by those which occur at highest levels, those for which information on related chemical properties suggests a possible health concern, or those chemicals which are more prevalent in regions of the country with the strongest relationship between the total chemical discharges and cancer mortality.
Second, the effects of co-exposures or mixtures of more than one chemical deserve further investigation. Most exposure research has focused on the effects of a single agent (lead, arsenic, benzo[a]pyrene, etc.), but there is increasing recognition that exposures to multiple agents simultaneously more closely matches what people actually experience in daily life , and that co-exposures may have additive or synergistic effects beyond single exposures, although research on this question is limited. The exposures in the current study were not isolated as to single agents because of the large number of possible agents to investigate and because release levels of any particular agent expressed on a national scale are usually small and are often concentrated in a few regions of the country.
Based on previous research, investigations of co-exposures may best be targeted initially to combinations of single agents about which there are known effects, especially when those agents are known to have similar health impacts such as manganese and lead co-exposure impacting neurodevelopment , or studies that investigate mixtures of single agents that are known individually to increase cancer risk such as arsenic , chromium(VI) , PAHs , tetrochloroethylene , or others.
Third, regional variations seen in the current study are intriguing but require future investigations to attempt to understand. The northern Great Plains area highlighted in
Figure 5 is one example. This area is largely rural and sparsely populated. It may be that rural areas, at least in some circumstances, are less impacted by environmental contaminants than urban areas, such that, when an environmental pollutant source (such as PCS discharges) is present in a rural area, that source represents a unique "spike" in exposures relative to background, whereas in urban areas with the same PCS pollutant source, the additional contribution of this source to health outcomes may be harder to detect against a background of other pollutants from industry or transportation.
Fourth, spatial variation in the contributions of area-weighted and on-site discharges suggests that area-weighted or upstream discharges may be important for some areas, whereas local discharges are more important for others (Figure 5). It is difficult to identify a pattern that can account for this variation; on-site discharges are relatively more important along the entire Mississippi River, but other major river systems don't show this pattern. Some major population centers are in areas where on-site discharges are more important, but other population centers are in areas where area-weighted scores had stronger effects. Regional variation in the composition of chemicals discharged may play a role in this spatial variation, as some chemicals or combinations of interacting chemicals may be present in one area but not in others. Regions to examine for these effects include the Northern Rockies and Arizona, where the measure of carcinogen releases instead of the non-carcinogen releases added substantial explanatory ability to the model, as well as areas in the Northern Plains and New England, which showed the strongest relationship between non-carcinogenic releases and cancer mortality. Similarly, there may be regional variation in how far downstream chemicals travel from the discharge site. Both properties of the chemical, such as its molecular weight, and properties of the stream, such as how fast it is flowing, could affect the distance the chemical travels. Accounting for molecular weight of airborne pollutants can improve models of atmospheric releases and public health outcomes , and a similar strategy may be useful when examining water-borne discharges.
Limits of the study include the ecological design, the selection of a partial list of chemicals with ingestion toxicity weights, the knowledge that the health impacts of mixtures are poorly understood, and the imperfect time relationships between discharges and mortality. Kidney disease was selected as one diagnostic sub-group for study but others, such as bladder cancer  could also have been investigated. We do not account for additional environmental variables that may be related to cancer or non-cancer risks, including geographic variation in levels of UV-B [20, 21], nitrates from non-point pollution agricultural sources , or traffic emissions. The results of the study must be taken as exploratory, but do show possible connections between greater permitted discharges of toxic chemicals into surface water and human health consequences, with potentially important geographic variations in the impacts of these discharges and in the particular discharges and health outcomes of greatest concern.
The study employs a county-level, ecological secondary data analysis. Dependent variables are population age-adjusted mortality rates (e.g., cancer mortality rates), and are statistically associated with independent variables (e.g., releases of carcinogens into surface waters) in the context of controlling for covariates (e.g., race/ethnicity, poverty rates, physician supply). Variables are described in further detail below.
The design also includes comparative findings for rural and urban areas. Counties were classified using the US Department of Agriculture's urban-influence codes (UICs) to identify metropolitan areas (codes 1 and 2), non-metropolitan areas adjacent to metropolitan areas (codes 3,4,5,6,7,9 and 10), and non-metropolitan areas not adjacent to metropolitan areas (codes 8,11 and12).
Data sources and variables
The EPA's Discharge Monitoring Report (DMR) database, which includes data from the Permit Compliance System (PCS) and the Integrated Compliance Information System - National Pollutant Discharge Elimination System (ICIS-NPDES), was used to measure the location, type, and quantity of water pollution discharges . The DMR database provides information on companies that have been issued permits to discharge wastewater into rivers or streams, including data on the amounts and types of chemicals discharged. An exported Oracle database was provided to us by the EPA containing the DMR data for the year 2007. The pollutant loading table in the database included 322,113 records of aggregate discharge measurements from 30,228 unique facilities. One thousand one hundred nine (1,109) parameters are included in the data, from basic water chemistry information (pH, temperature, etc) to concentrations of various compounds classified as "pollutants" by the EPA (n = 729). Not all records contain values for all parameters; each record contains values for one parameter, relevant to that facilities' permit. Of the pollutants, a total of 518 unique Chemical Abstract Service (CAS) registry numbers were identified in the data. Of those 518 CAS registry numbers, we initially limited the analysis to discharges of 73 chemicals selected based on their possible human health impacts. We chose a subset of chemicals rather than attempting to use all chemicals because of the extensive time demands required to find, clean, and aggregate chemical-specific discharge data across the 322,113 discharge records in the DMR data. Selecting only those records containing a chemical of interest left us with 55,183 records. We also limited the data points used in the analysis by removing all records with a release value across all chemicals of interest of zero (n = 20,948). Next, we removed all records that fell outside of the contiguous United States (n = 13,197), and all records whose latitude/longitude coordinate fields contained values of "0" or other anomalous values (n = 143). Finally, we removed all records wherein a single facility listed the same discharge value for all releases as this was clearly reported in error (n = 56). Once these edits were completed, we were left with a database of 19,824 permitted discharges from 10,395 individual facilities which were used in development of subsequent analyses.
To aggregate discharges from upstream sources into downstream geographic areas, we utilized the Watershed Boundary Dataset, a multi-level spatial dataset for watersheds created and maintained by the Natural Resource Conservation Service (NRCS) and published as part of the National Hydrography Dataset (NHD) . The data were downloaded from the NHD server as a single file for the United States. We extracted the Sixth level (12 digit) watershed and checked the relevant upstream and downstream fields within the database to ensure that we could connect the upstream to downstream flows. Finally, we summed the discharges per chemical within each watershed for use in later analysis and aggregation.
Toxicity weighted and un-weighted discharges
List of chemicals used in analyses
For toxicity weighted analyses, the values for each chemical were multiplied by the weight for that chemical. Toxicity weighted and unweighted quantities for each county were then summed across all carcinogens, and again across all non-carcinogen chemicals. Amounts of these summed chemical discharges were not normally distributed across counties, so we calculated the natural log of discharge amounts for analysis. All discharges are expressed as the log of kg per year.
Onsite and area-weighted upstream discharges
Here, π s is the pollution score for the watershed, ρ w is the summed releases for that watershed, w ≥ s denotes all watersheds upstream of shed s, including shed s itself, and area w→S denotes the area in acres of all watersheds between sheds w and s, including both w and s. When w = s, this reduces to the area of that watershed. We employ this reduction to account for the likelihood that releases far upstream of a location will have less influence on that location than nearby releases.
Population-weighted county-level discharges for both onsite and areas-weighted upstream discharges
Here, s is a watershed, c is the county, pop s, c is the estimated population in the watershed/county intersection, π s is the pollution score for the watershed, and e c is the total exposure score for the county. The denominator of the fraction is simply the population of the county, but is shown as the sum of the population of all watershed/county intersections to illustrate the weighted average nature of the calculation. We calculated values for both onsite and area-weighted exposures. The onsite calculation replaces π s with the release variable ρ s .
Health outcome data were drawn from the public CDC mortality files for the years 2003-2007. We selected a five-year aggregate period to acquire more stable estimates than would be possible by selecting only one year, and choose the most recent five-year period available from the CDC at the time of the study, recognizing that this creates an imperfect match between the mortality observation period and the chemical discharge period. We are forced to assume that PCS discharge quantities at the county level are stable over time, such that later discharges provide a reasonable estimate of earlier discharges.
From the CDC we found the annual age-adjusted mortality rates per 100,000 for 1) all cancer (ICD-10 codes C00-C97 malignant neoplasms); 2) chronic or unspecified non-cancer kidney disease (ICD-10 diagnostic GR113 codes 99, 100 and 101; the uncommon code 98 reflecting 'acute and rapidly progressive' disease was excluded); and 3) all non-cancer mortality causes causes combined, excluding accidents, suicide and homicide. Kidney disease was selected as one category because of previous research suggesting that kidney disease may be particularly sensitive to exposure to water pollutants, especially heavy metals [28–31]. Rates were age-adjusted using the standard 2000 US Census population.
Other variables were measured from the 2007 Area Resource File and CDC 2006 Behavioral Risk Factor Surveillance System (BRFSS) survey data. Covariates include county-level measures of adult smoking rates, college education rates, poverty rates, race/ethnicity percentages, physician per capita supply, and adult obesity rates.
Onsite discharges not toxicity weighted
Onsite discharges with toxicity weights
Area weighted upstream discharges with toxicity weights
Area weighted upstream discharges with toxicity weights cross-validated.
Area weighted upstream discharges with toxicity weights separately for metropolitan, non-metropolitan adjacent, and non-metropolitan non-adjacent counties
Area weighted carcinogen releases, toxicity weighted
Area weighted carcinogen releases, not toxicity weighted
Area weighted non-carcinogen releases, toxicity weighted
Onsite carcinogen releases, toxicity weighted
Onsite carcinogen releases not toxicity weighted
Onsite non-carcinogen releases, toxicity weighted
Onsite non-carcinogen releases not toxicity weighted
The eighth possible analysis, using the area weighted non-carcinogen releases, not toxicity weighted, was not completed because the GWR failed to evaluate because of local multicollinearity errors, even when the number of neighbors was increased to 300 counties. We did not examine the geographic patterns of kidney mortality because the suppression of some counties' data due to small numbers of cases precluded spatial analysis. We decided to limit the spatial analysis to cancer mortality to conserve space, but results for non-cancer mortality are briefly described in text in the Results section.
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