- freely available
Int. J. Environ. Res. Public Health 2014, 11(2), 1803-1823; doi:10.3390/ijerph110201803
Abstract: Animal studies and epidemiological evidence suggest an association between prenatal exposure to drinking water with elevated nitrate (NO3-N) concentrations and incidence of congenital anomalies. This study used Geographic Information Systems (GIS) to derive individual-level prenatal drinking-water nitrate exposure estimates from measured nitrate concentrations from 140 temporally monitored private wells and 6 municipal water supplies. Cases of major congenital anomalies in Kings County, Nova Scotia, Canada, between 1988 and 2006 were selected from province-wide population-based perinatal surveillance databases and matched to controls from the same databases. Unconditional multivariable logistic regression was performed to test for an association between drinking-water nitrate exposure and congenital anomalies after adjusting for clinically relevant risk factors. Employing all nitrate data there was a trend toward increased risk of congenital anomalies for increased nitrate exposure levels though this was not statistically significant. After stratification of the data by conception before or after folic acid supplementation, an increased risk of congenital anomalies for nitrate exposure of 1.5–5.56 mg/L (2.44; 1.05–5.66) and a trend toward increased risk for >5.56 mg/L (2.25; 0.92–5.52) was found. Though the study is likely underpowered, these results suggest that drinking-water nitrate exposure may contribute to increased risk of congenital anomalies at levels below the current Canadian maximum allowable concentration.
Congenital anomalies complicate 2% to 3% of Canadian births and the incidence of neural tube defects, congenital heart defects and Down’s syndrome in Nova Scotia are among the highest in Canada . The etiologies of many congenital anomalies remain unknown; their widespread health impacts warrant further investigation into risk factors, environmental causes and means of prevention .
Teratogens in the environment, such as nitrate, may cause 8%–12% of congenital anomalies [1,2]. Nitrate (NO3) is one of the most prevalent forms of biologically-available nitrogen, and may be created naturally or anthropogenically [3,4,5]. Nitrate is soluble in water and has the ability to leach into groundwater [3,4,5].
Ingested nitrate may be converted to nitrite by microbial reduction in saliva, or in the stomach during instances of increased pH or infections with diarrhea-producing bacteria [6,7]. Nitrites can react with amines and other nitrosatable compounds to produce highly reactive N-nitroso compounds in the stomach [6,7]. Several animal studies have shown that nitrates and other nitrogenous compounds can cross the placenta and have a teratogenic effect on the developing fetus during pregnancy, particularly impacting the central nervous system [8,9,10]. Several case-control studies have shown a positive association between drinking-water nitrate levels and incidence of congenital anomalies among humans [11,12,13,14,15]. Dorsch et al. showed increased risk of all congenital anomalies for nitrate concentrations >5 mg/L . Arbuckle et al. showed an increased risk of central nervous system (CNS) anomalies in New Brunswick, Canada, for nitrate concentrations >26 mg/L and Croen et al. showed an increased risk of anencephaly for those whose mothers drank groundwater with nitrate concentrations >6.9 mg/L [12,13]. Studies by Cedergren et al. and Manassaram et al. showed trends toward associations between drinking-water nitrate and anomalies of the cardiac and central nervous systems respectively [14,15].
This study was designed to estimate the association between drinking-water nitrate concentrations and incidence of major congenital anomalies in the agricultural region of Kings County, Nova Scotia, Canada. It expanded on existing research in four main ways: (1) the use of province-wide population-based databases enabled controlling for a number of health and demographic variables that may confound the association between drinking-water nitrate and congenital anomalies; (2) we were able to include cases diagnosed in-utero with congenital anomalies in pregnancies that were electively terminated before birth; (3) we included users of both private wells and municipal water supplies in the study population and; (4) individual-level nitrate exposure estimates were derived from temporally monitored well data with fine geographic resolution, using Geographic Information Systems (GIS), providing confidence in these estimates.
2. Experimental Section
2.1. Research Ethics Board Approvals
To ensure confidentiality, the Reproductive Care Program of Nova Scotia selected cases and controls using the selection criteria described below. Approval for access to data in the Nova Scotia Atlee Perinatal Database (NSAPD) was granted by the Data Access Committee of the Perinatal Epidemiology Research Unit, the Dalhousie University Population Health Research Unit, and the Reproductive Care Program of Nova Scotia. Approval for the use of data in the Dalhousie University Department of Obstetrics and Gynecology Fetal Anomaly Database (FAD) was granted by the FAD Data Access Committee. The project received ethical approval from the IWK Health Centre Research Ethics Board and the Annapolis District Health Authority Research Ethics Board.
2.2. Study Area
The study was undertaken in Kings County (total 2,001 population = 58,866) located in the predominantly agricultural Annapolis Valley, in South-Western Nova Scotia, a province in Eastern Canada. Kings County was selected because a series of wells along the intensively-farmed valley floor have had routine nitrate concentrations measured repeatedly in 1989, 1999 and 2000 to examine seasonal and temporal variations. Water quality in Kings County is usually good, though it is susceptible to contamination from surficial sources along the valley floor [10,16,17]. In 1999, 44% of the 140 wells sampled in the study area had nitrate-nitrogen concentrations (hereafter referred to as nitrate concentration) above 5 mg/L, and 19% had nitrate concentrations above the 10 mg/L Health Canada Maximum Allowable Concentration (MAC) . Kings County includes the municipalities of Canning, Wolfville, Kentville, New Minas, and Port Williams. Each municipality has its own water supply described in Table 1 [18,19,20,21].
|Location||Water Source||# of Sample Locations||Total # of Samples||Min. [Nitrate]||Max. [Nitrate]||Mean [Nitrate] *||Median [Nitrate)||Nitrate Exposure Level|
|All rural wells||Groundwater||140||1,113||0.0||43.0||6.44|
|All municipalities||Ground and surface water||20||53||0.0||10.4||2.03|
Note: * 95% CI.
2.3. Data Sources
All cases and controls were selected from either the NSAPD or FAD. The NSAPD was established in 1988 and is a province-wide population-based birth registry database. The NSAPD contains systematically-recorded information on maternal and infant demographics, as well as information on medical procedures, interventions, diagnoses (including congenital anomalies) and health outcomes for all births in Nova Scotia. This information is recorded through a formal coding process at a central location. Data are obtained from hospital records, physician reports, prenatal diagnostic facilities, cytogenetic laboratories, maternal serum screening programs and vital statistics. The FAD was established in 1992 and records information on all Nova Scotia fetal anomalies diagnosed during pregnancy, including those pregnancies that underwent second trimester terminations. FAD data are obtained in similar fashion as is done for the NSAPD. Linkages between the NSAPD and the FAD are made using Nova Scotia provincial health card numbers.
Latitude and longitude of maternal addresses were determined using the Nova Scotia Civic Address File, which was introduced province-wide in 1998 to support the implementation of the provincial Emergency Health Service. The latitude and longitude of the centre-point of every dwelling in Nova Scotia has been measured using a handheld GPS unit, resulting in location estimates that are accurate within 2.5 m , and recorded in a central spatial database for use in response to 911 emergency calls.
2.4. Inclusion and Exclusion Criteria
All fetuses or infants diagnosed with a major congenital anomaly between 1 January 1988 and 31 December 2006 with a maternal residential address within the Kings County boundaries were selected as cases. Infants born without a major congenital anomaly over the same time period, also with a maternal residential address within the Kings County boundaries were selected as controls. Cases and controls were matched at a 1:3 ratio based on infant’s sex and date of conception (within +/− 30 days) to enhance statistical power. For all cases and controls, the maternal address had to be available and in Kings County at the time of delivery. Twins and higher-order multiple births were excluded from the study. Principally an agricultural region, residential mobility is low in Kings County compared to Nova Scotia as a whole.
2.5. Demographic and Health Data Collection
In addition to the sex of the infant and season of conception (Spring: 20 March–20 June; Summer: 21 June–21 September; Fall: 22 September–20 December; Winter: 21 December–19 March), maternal demographic variables and information regarding maternal risk factors for congenital anomalies was obtained from the NSAPD and the FAD. These include: maternal age at conception, maternal parity (defined as the number of times a woman had given birth to an infant or stillbirth having a gestational age of 20 weeks or more, or having a birthweight of 500 grams or more), smoking (either pre-pregnancy or at first prenatal visit), pre-existing or gestational diabetes, pre-existing thyroid disease, patient-reported folate supplementation at the time of conception, patient-reported pre-pregnancy weight, and conception before or after folate fortification in Nova Scotia (determined by month and year of conception).
2.6. Nitrate Concentration Measurement
For study participants residing in regions served by municipal water supplies, nitrate exposure estimates were based on water system nitrate concentrations measured between 1996 and 2003 provided by each of the six water supply plants (Figure 1). At these plants, water samples were taken with variable frequencies and at irregular intervals over the study period. For the municipal water supplies as an aggregate, analyses were conducted to evaluate the variation in nitrate concentration over time in each municipality. Linear mixed effects models were used to assess the effects of location of the sample (if samples were drawn from multiple locations within a single municipality), month of sample, and year of sample on log-transformed nitrate concentrations.
Sample location was considered a random effect, while month of sample and year of sample were considered fixed effects. Similar methods have previously been used to assess temporal changes in groundwater nitrate measurements [23,24]. Year and month of the water samples from the municipal water supplies were not significantly associated with nitrate concentration (Year: p = 0.92, Month: p = 0.38). Sample location alone described most of the variation in nitrate levels (R2 = 0.74, p < 0.01). Therefore, the median of all nitrate concentration measurements taken within each municipal water supply was used as the nitrate exposure estimate for all study participants living in each municipality (Figure 2).
In rural areas, drinking-water nitrate concentrations were estimated using GIS (see below) from the nitrate concentrations of monthly samples taken from 140 wells in 1999 and 2000. These wells were among 237 originally selected for routine monitoring by the Nova Scotia Department of Environment and Labour and the Nova Scotia Agricultural College according to the DRASTIC model in 1989. The DRASTIC model integrated information regarding the location of various agricultural crops and soils to estimate susceptibility to nitrate contamination beyond the natural background level [25,26]. Wells were selected such that they represented a range of susceptibilities toward nitrate contamination . Monitoring took place monthly from July 1999 to February 2000. Linear mixed effects modeling was used to evaluate the variation in nitrate concentrations between wells, as well as variation in nitrate concentration of the water from each well for different months and years. The year and month in which the water samples were taken were not associated with nitrate concentration (Year: p = 0.61; Month: p = 0.12) and well location described most of the variation in nitrate in rural areas (R2 = 0.74, p < 0.01). Therefore, a single map representing rural nitrate concentration estimates based on location of wells was created.
2.7. Exposure Assessment
The exposure assessment for participants in our study was conducted using ArcGIS software (ESRI, Redlands, CA, USA). First, ordinary kriging was used to estimate nitrate concentrations in areas near the 140 monitored wells. The final spatial resolution of the derived raster surface was 1:2.2 with a cell size of 221 m. This model was then extrapolated to cover all of Kings County. For details of the kriging and extrapolation process used to estimate nitrate exposure in rural areas see the supplementary material. All interpolation models considered, as well as their parameters and associated errors are included in Table S1. Next, maps delineating the service boundaries of each municipal water supply were used to draw freehand polygons representing the geographic range of each water supply distribution system in ArcGISTM. Lists of addresses served by each municipality were used to confirm the accuracy of the polygons, which were cross-checked by each water supply manager. Next, the regions served by municipal water supplies were “cut-out” from the map representing rural nitrate concentrations and the median value of all nitrate measurements for each municipal water supply was imputed into the appropriate polygon. The latitude and longitude of the maternal address at the time of delivery was then used to determine a nitrate-exposure estimate for each study participant.
The nitrate concentration estimates (represented as mg nitrate-nitrogen) were divided into drinking-water nitrate exposure level categories (<1 mg/L, 1–5.56 mg/L, >5.56 mg/L), with 1 mg/L demarcating pristine areas from anthropogenically-affected areas in Atlantic Canada and 5.56 mg/L consistent with the European guideline for a “safe” level of nitrate in drinking-water [27,28].
2.8. Statistical Analyses
Frequency tables and univariable analyses using unconditional logistic regression were created for all covariates included in the study (infant sex, season of conception, year of conception, maternal age, maternal parity, pre-pregnancy weight, smoking, thyroid disease, diabetes, folate supplementation, folate fortification, ground vs. surface water, municipal vs. private water supply, and nitrate exposure). A step-wise multivariable unconditional logistic regression, including those variables on which the study participants were matched, was used to estimate the odds ratios (OR) and 95% confidence intervals (95% CI) for the incidence of congenital anomalies by drinking-water nitrate exposure level. Since study participants were matched on very few parameters relative to the total sample size, unconditional logistic regression was used to examine associations in this study.
Covariates were added to the multivariable model by group in a stepwise fashion in order to assess their impacts on the association between drinking-water nitrate and congenital anomalies. Groups of covariates were added to the model in the following order: (1) matching variables (sex, season of conception, year of conception); (2) demographic variables (maternal age, parity); (3) maternal risk factors (smoking, diabetes, thyroid disease); (4) water source variables (surface vs. groundwater, municipal vs. rural) and finally; (5) nitrate exposure level. This process enables stepwise comparison of the impact of the addition of each set of covariates to the overall point estimates and confidence intervals for previously introduced parameters. The final column shows the results from the nitrate exposure levels after all previous variables of interest are accounted for.
The logistic regression analyses were repeated after stratifying the data by date of conception before or after 1 January 1998. The year 1998 was chosen as the year of stratification because it is the year in which Canada first began to fortify food containing grain with folic acid nationally for the purpose of ensuring pregnant women were receiving sufficient quantities in their diets. It also coincides with the introduction of civic geocoding (exact latitude and longitude) of all addresses of all homes in Nova Scotia thereby enhancing accuracy of geographic location where the estimated exposures occurred.
3. Results and Discussion
Descriptive statistics for the nitrate measurements for the rural wells in aggregate, as well as all six municipal water supplies, are shown in Table 1. The mean and median drinking-water nitrate levels were below the MAC in both municipalities and rural areas, though the mean, median and maximum drinking-water nitrate concentrations were higher in rural areas compared to those within municipalities. Some nitrate measurements from rural wells, as well as at least one from the municipality of Port Williams, were above the MAC.
Frequency of congenital anomalies by body system for the entire study period, as well as stratified for before and after 1998, are presented in Table 2. Congenital anomalies of the central nervous system were the most common throughout the entire study period.
|Class of Anomaly||Entire Study Period||Before Folate Fortification||After Folate Fortification|
|Number of cases||Percentage of all congenital anomalies||Number of cases||Percentage of all congenital anomalies for period||Number of cases||Percentage of all congenital anomalies for period|
|Central Nervous System||286||47||98||33||188||61|
|Eye, Ear, Nose, Throat and Mouth||27||4||17||6||10||3|
Note: * All categories containing fewer than five cases were amalgamated.
Frequency tables and odds ratios comparing cases to controls for covariates, as well as nitrate exposure estimates are summarized in Table 3. There was an increased likelihood of congenital anomalies with maternal smoking and a protective effect shown for maternal parity of 1–2. Provision of water from a private or municipal water supply, ground or surface water source, and drinking-water nitrate exposure level did not differ between cases and controls.
|Variable||Cases (n = 606)||Controls (n = 1,635)||Crude Odds Ratio **||p-value *|
|Season of conception||0.96|
|Year of Conception|
|Pre-pregnancy weight (kg)||0.55|
|Nitrate exposure level|
|1–5.56 mg/L||351||58||931||57||1.02 (0.81–1.30)||0.68|
|>5.56 mg/L||127||21||351||21||0.97 (0.73–1.29)||0.71|
Notes: * The values listed across from the variable names represent the p-values for the entire model. The p-values listed across from each category within variables represent the p-values for that category. ** 95% CI.
Table 4 summarizes the step-wise multivariable unconditional logistic regression model comparing cases to controls, without variables representing folic acid supplementation and pre-pregnancy weight, which were removed due to large numbers of missing data (68% and 21% respectively). After controlling for all other variables there is a trend-toward a modest increase in risk of congenital anomalies with exposure to nitrate concentrations greater than 1 mg/L, which is the local background nitrate concentration. This trend was present for both exposure categories 1–5.56 mg/L and >5.56 mg/L. However, this categorical nitrate variable does not attain statistical significance or show a dose-response relationship.
|Variable||Basic Model: Matching Variables||Basic Model Plus Maternal Demographic Variables||Basic Model Plus Maternal Demographic and Health Variables||Basic Model Plus Maternal Demographic, Health and Water Source Variables||Final Model: Effect of Nitrate Exposure Level on Congenital Anomalies after Controlling for All Other Variables|
|Male||0.99 (0.82–1.20)||0.99 (0.82–1.21)||0.98 (0.81–1.20)||0.99 (0.81–1.20)||0.98 (0.81–1.20)|
|Season of conception|
|Spring||1.04 (0.76–1.43)||1.05 (0.76–1.44)||1.05 (0.76–1.44)||1.05 (0.76–1.44)||1.05 (0.76–1.44)|
|Summer||0.97 (0.72–1.34)||0.99 (0.72–1.34)||1.00 (0.73–1.37)||1.00 (0.74–1.37)||1.00 (0.74–1.37)|
|Fall||0.97 (0.72–1.32)||0.96 (0.72–1.27)||0.97 (0.71–1.32)||0.97 (0.71–1.32)||0.98 (0.72–1.33)|
|Year of conception|
|1992–1996||0.98 (0.71–1.36)||0.97 (0.70–1.36)||0.98 (0.71–1.37)||0.99 (0.71–1.38)||0.99 (0.71–1.38)|
|1997–2001||1.00 (0.71–1.36)||0.96 (0.72–1.27)||0.97 (0.73–1.29)||0.98 (0.74–1.31)||1.00 (0.75–1.34)|
|2002–2006||1.05 (0.73–1.51)||1.02 (0.70–1.45)||1.02 (0.71–1.48)||1.03 (0.72–1.49)||1.05 (0.72–1.52)|
|<20||1.01 (0.71–1.44)||0.94 (0.66–1.35)||0.94 (0.66–1.35)||0.95 (0.66–1.36)|
|≥35||1.38 (1.01–1.88)||1.40 (1.02–1.91)||1.39 (1.02–1.91)||1.40 (1.02–1.91)|
|1–2||0.73 (0.60–0.90)||0.73 (0.59–0.89)||0.73 (0.59–0.89)||0.73 (0.60–0.90)|
|3+||0.68 (0.43–1.07)||0.67 (0.43–1.06)||0.68 (0.43–1.07)||0.70 (0.43–1.06)|
|Yes||1.28 (1.03–1.57)||1.28 (1.03–1.57)||1.27 (1.03–1.57)|
|Gestational||1.30 (0.70–2.41)||1.29 (0.70–2.40)||1.31 (0.71–2.44)|
|Other diabetes||0.97 (0.34–2.73)||0.97 (0.34–2.73)||0.96 (0.34–2.70)|
|Yes||0.64 (0.14–3.00)||0.65 (0.14–3.05)||0.64 (0.14–3.01)|
|Ground||0.85 (0.66–1.09)||0.70 (0.35–1.41)|
|No||1.10 (0.81–1.51)||0.82 (0.63–1.07)|
|Nitrate exposure level|
|1–5.56 mg/L||1.65 (0.83–3.27)|
|>5.56 mg/L||1.66 (0.81–3.42)|
The data were then stratified by date of conception before or after 1 January 1998 (Table 5). For cases and controls conceived prior to 1998, there appeared to be a non-significant protective effect for exposure to drinking-water nitrate concentrations greater than 1mg/L. A trend toward reduced risk of congenital anomalies with nitrate exposure greater than the background concentration was shown for both nitrate exposure categories (1–5.56 mg/L and >5.56 mg/L.) For cases and controls conceived after 1998 there was a significantly increased risk of congenital anomalies with nitrate exposure from 1–5.56 mg/L and a trend toward an increased risk of congenital anomalies with nitrate exposure greater than 5.56 mg/L. For cases and controls selected after 1998, the effect size was slightly larger for the 1–5.56 mg/L than the >5.56 mg/L exposure level.
This study builds on previous work to examine the association between drinking-water nitrate concentrations and incidence of major congenital anomalies in the agricultural region of Kings County, Nova Scotia, Canada by employing the use of province-wide population-based birth registry data which enabled controlling for factors that may have introduced confounding in previous studies and which allowed for inclusion of cases diagnosed in-utero with congenital anomalies in pregnancies that had been electively terminated before birth. This study also included users of both private wells and municipal water supplies in the study population and made use of county-wide groundwater nitrate seasonal surveys of concentrations and GIS methods to derive spatial estimates of individual-level nitrate exposure.
|Variable||Cases and Controls Conceived from 1987–1997|
(n = 987)
|Cases and Controls Conceived from 1998–2006|
(n = 1,201)
|Male||1.0 (0.75–1.34)||0.96 (0.73–1.24)|
|Season of conception|
|Spring||1.0 (0.61–1.63)||1.12 (0.73–1.71)|
|Summer||1.01 (0.62–1.63)||1.01 (0.67–1.53)|
|Fall||0.98 (0.62–1.55)||0.98 (0.64–1.50)|
|Year of conception|
|<20||0.85 (0.50–1.43)||1.01 (0.61–1.68)|
|≥35||1.35 (0.76–2.39)||1.50 (1.03–2.19)|
|1–2||0.77 (0.56–1.05)||0.68 (0.52–0.90)|
|3+||0.75 (0.39–1.45)||0.59 (0.31–1.11)|
|Yes||1.01 (0.74–1.38)||1.55 (1.16–2.06)|
|Yes||1.55 (0.13–18.10)||0.36 (0.04–3.01)|
|Gestational||1.63 (0.73–3.64)||2.27 (0.30–16.71)|
|Other diabetes||0.49 (0.06–4.15)||–|
|Ground||2.50 (0.62–10.08)||0.54 (0.23–1.29)|
|No||0.78 (0.53–1.14)||0.82 (0.56–1.20)|
|Nitrate Exposure level|
|1–5.56 mg/L||0.48 (0.10–1.60)||2.44 (1.05–5.66)|
|>5.56 mg/L||0.47 (0.11–1.90)||2.25 (0.92–5.52)|
This study found that in univariable logistic regression analyses there was an increased risk of congenital anomalies with maternal smoking, and a protective effect with maternal parity of 1–2 (Table 3). Some previous studies have shown positive associations between smoking and congenital anomalies , though others have shown no association [30,31]. Previous studies have found that primiparity, especially in combination with older age and higher pre-pregnancy weight, is a significant risk factor for congenital anomalies [32,33]. Univariable analyses showed no effect of folic acid supplementation or fortification on incidence of congenital anomalies. Previous work in Nova Scotia has also shown that recommendations for folic acid supplementation had only a limited effect on incidence of neural tube defects, but that the incidence of neural tube defects was reduced after folic acid fortification . It is likely that the onset of folic acid fortification showed no protective effect against congenital anomalies in this study because the analysis examined all major congenital anomalies, rather than exclusively neural tube defects, which are specifically associated with folic acid intake.
Using reliable outcome and covariate database, and a reasonably robust interpolated exposure variable, we were able to identify a trend (OR = 2.44) toward a positive association between congenital anomalies and drinking-water nitrate for the period 1998–2006, even while controlling for important cofounders (Table 5). When the study period as a whole is considered, there was a trend toward an increase in incidence of congenital anomalies with drinking-water nitrate exposure of 1–5.56 mg/L and >5.56 mg/L. When the data were stratified by conception before or after 1998, there was a non-significant protective effect for drinking-water nitrate exposure of 1–5.56 mg/L and >5.56 mg/L. This result was reversed for the cases and controls conceived after 1998, where there was a significant positive association between drinking-water nitrate levels from 1–5.56 mg/L and a non-significant positive association, though of slightly less magnitude, for drinking-water nitrate levels greater than 5.56 mg/L.
The trend toward a positive association between congenital anomalies and drinking-water nitrate is consistent with previous studies. Dorsch et al. found that women who consumed water with total nitrate-nitrogen concentrations between 5 mg/L and 15 mg/L were 2.6 times more likely than women who consumed water with total nitrate-nitrogen concentrations below 5 mg/L to give birth to a child with a congenital anomaly (RR = 2.6, 95% CI = 1.6–4.1); those who consumed water with total nitrate-nitrogen concentrations above 15 mg/L experienced a 4.1 times greater risk of anomaly (RR = 4.1, 95% CI = 1.3–13.1) . Arbuckle et al. observed that total nitrate-nitrogen concentrations of 26 mg/L showed a moderate increase in risk of CNS anomalies (ROR = 2.3; 95% CI = 0.73–7.29) when well water was considered in isolation . Croen et al. (2001) found a progressively increased risk of anencephaly according to higher levels of total nitrate-nitrogen exposure for groundwater drinkers only (OR = 2.1; 95% CI = 1.1–4.0 for exposure concentrations of 5–15 mg/L; OR = 2.3; 95% CI = 1.1–4.5 for exposure concentrations of 16–35 mg/L; OR = 6.9; 95% CI = 1.9–24.9 for exposure concentrations of 36–67 mg/L) . Cedergren et al. found that infants exposed in-utero to more than 2 mg/L nitrate-nitrogen had a marginally elevated risk of cardiac defects (OR = 1.18, 95% CI = 0.97–1.44) .
It is unclear why there appeared to be a protective association between drinking-water nitrate concentration and congenital anomalies before 1998 but an in increased risk with elevated drinking-water nitrate after 1998. There are several factors that may have contributed to this finding. The Nova Scotia Civic Address File was introduced in 1998, which likely improved the nitrate exposure classification of cases and controls from 1998 onward. Increased precision of addressing likely reduced random misclassification of nitrate exposure estimate and would have increased the power of the study to detect differences in incidence of congenital anomalies between drinking-water nitrate exposure groups.
It is also possible that the reversal of the relationship between nitrate exposure and incidence of congenital anomalies for before and after 1998 is related to the fortification of grain products with folic acid in order to protect against neural tube defects. Our study examined all congenital anomalies, the majority of which were central nervous system anomalies, which includes neural tube defects. Both before and after 1998, congenital anomalies of the central nervous system were the most prominent type of congenital anomalies in Kings County. It is plausible that since prior to 1998, a large portion of the risk of congenital anomalies could be attributed to insufficient folic acid intake, and once this risk was abated after folic acid fortification the risk of congenital anomalies due to nitrate exposure was unmasked.
Our study did not find evidence for a dose-response relationship between incidence of congenital anomalies and drinking-water nitrate exposure level; the odds ratio was higher for the lower exposure category (1–5.56 mg/L) than for the higher exposure category (>5.56 mg/L). This may be due to limited power to detect a difference at the higher exposure level, as there were only 21 cases and controls in this group.
3.2.1. Study Strengths
This study is unique because participants were selected from population-based databases that included data on elective second-trimester termination of pregnancies with antenatally diagnosed congenital anomalies, providing very complete case ascertainment. The wealth of high-quality information on maternal demographic and risk factors contained in the population-based databases also enabled controlling for a large number of maternal risk-factor for congenital anomalies, which enabled a more precise evaluation of the association between nitrates and congenital anomalies.
Access to the Nova Scotia Civic Address file, which provided a precise latitude and longitude designation for all maternal addresses after 1998 also reduced likelihood of exposure misclassification due to false geographic location for the study period from 1998 onward. The robustness of the nitrate exposure variable was also enhanced by including users of both private wells and municipal water supplies in the study population and temporally monitored well data with fine geographic resolution using GIS.
3.2.2. Study Limitations
The primary limitation of this study was that there were not sufficient cases for analyses to be sub-divided according to specific type of congenital anomalies. Environmental teratogens are expected to exert specific effects, contributing to the development of a relatively narrow range of congenital anomalies .
Another limitation of the study is that in rural areas the drinking-water nitrate exposure estimates were based on a study which took samples only in 1999 and 2000. Therefore, some water samples were taken after the birth of cases and controls. Too little data was available to reliably assess the temporal stability of drinking-water nitrate concentrations over the entire study period from 1987 to 2006. The study relied on linear mixed effects models to determine that sample location contributed to the most variation in drinking-water nitrate in Kings County over the study period. However, the trends in nitrate concentrations in Kings County found in our study are generally consistent with the existing literature. Previous work by Moerman and Briggins found that 13% of 237 wells in Kings County had nitrate concentrations greater than the MAC in 1989, which was similar to nitrate concentrations in Kings County in 1974 . Work by Blair et al. using the same data at our study set also showed no monthly variation in nitrate concentrations. However, they did find that nitrate concentrations were higher in 1999 than in either 1989 or 2000 . The work of both Moerman and Blair found elevated nitrate concentrations in Eastern Kings County bordering Canning and Port Williams, which is consistent with our nitrate exposure model [38,39].
The choice of ordinary kriging to model nitrate exposures in rural Kings County may have also limited the quality of the drinking-water nitrate exposure estimates. Kriging performs poorly when sample points are sparse , as is the case in the Western part of Kings County. Furthermore, our model was extrapolated to include all of Kings County, while all of the nitrate sampling points from both rural wells and municipal water supplies were located along the valley-floor. Outside the valley floor, nitrate concentrations were extrapolated. Overall, 72% of all civic address points in Kings County are in municipalities or in areas where the nitrate exposure model was represented by kriging. However, among Kings County residents using private wells to obtain drinking-water, 39% live outside the regions represented by kriging or municipal water supplies. Study participants living at these addresses had their nitrate exposure levels represented by an extrapolation of the kriging model, likely a poor representation of actual nitrate exposure. Therefore, there was likely some non-random exposure misclassification with more accurate nitrate exposure estimates made for those living along the valley floor than elsewhere in the study region.
Previous research in Kings County has found that those wells that have drinking-water nitrate levels that exceed the MAC are also more likely to contain fecal coliform bacteria and pesticides . In general, a high nitrate concentration in a well is indicative of the additional presence of other contaminants. This study may be limited by residual confounding because the presence of other drinking-water contaminants that may be correlated with high nitrate concentrations were not evaluated. For example, pesticides exposure may be associated with increased incidence of congenital anomalies and is also positively correlated with nitrate concentrations [23,36].
This study builds on the existing research on drinking-water nitrate exposure and congenital anomalies by using a population-based, enhanced birth surveillance program for ascertainment of cases and controls and for controlling for important maternal and infant congenital anomaly-related risk factors. Over the entire study period there was a non-significant small increase in risk of congenital anomalies for drinking-water nitrate levels >1 mg/L. When only data from 1998 onward was considered, there was a significant increase in the incidence of congenital anomalies for drinking-water nitrate exposure levels of 1–5.56 mg/L compared to <1 mg/L. There was not a dose response relationship when nitrate levels >5.56 mg/L were considered, possibly due to inadequate power. The observed increase in the incidence of congenital anomalies with drinking-water nitrate exposure greater than 1 mg/L, which is just 10% of the Canadian MAC, is an intriguing finding and suggests that further investigation of the relationship between drinking-water nitrate and congenital anomalies at lower exposure levels is warranted.
List of Abbreviations
Central Nervous System
Fetal Anomaly Database
Geographic Information Systems
Maximum Allowable Concentration
Nova Scotia Atlee Perinatal Database
Many organizations were involved in data acquisition for this project. We would like to thank the managers of the The Reproductive Care Program of Nova Scotia, The Fetal Anomaly Database, The Nova Scotia Department of Environment and Labour, The municipal water commissions of Canning, Kentville, the Municipality of the County of Kings, New Minas, Port Williams, Wolfville, The Kings County Community Health Boards and the IWK Health Centre. Special thanks for Richard Gould and Grant Ferguson for their assistance with the study design, as well as to John Fahey for compiling the data used in the study. Caitlin Holtby was the recipient of a Nova Scotia Health Research Foundation Graduate Fellowship Award and an Atlantic RURAL Centre Graduate Fellowship Award. This project was supported by the Atlantic RURAL Centre, enabled through Canadian Institutes of Health Research Grant number CDA-66534 (Judith R. Guernsey, Principal Investigator).
Dr. Caitlin Holtby was principally responsible for the study management and implementation which served as her Master's thesis. She contributed to the methological design of the study, constructed the data files, completed the data analyses and mapping for both statistical modelling and GIS components, and wrote the initial draft of the manuscript. Dr. Judith Guernsey conceived the idea for the study and served as Dr. Holtby’s thesis supervisor. She also contributed to the methodological design of the study and the manuscript. Drs. Alexander Allen, John Van Leeuwen, Victoria Allen and Robert Gordon contributed to the methodological design of the study and to the interpretation of findings and served as thesis committee members, Drs Allen and Allen facilitated access to, and provided clinical interpretation of the Perinatal Epidemiological Database. Dr.Robert Gordon also provided nitrate data for the rural wells and shared important contextual information related to the groundwater chemistry of nitrate concentrations in the Annapolis Valley of Nova Scotia. All authors approved the final manuscript.
Conflicts of Interest
The authors declare no conflict of interest
- Congenital Anomalies in Canada; Health Canada: Ottawa, Canada, 2002; pp. 1–87.
- Dodds, L.; Seviour, R. Congenital anomalies and other birth outcomes among infants born to women living near a hazardous waste site in Sydney, Nova Scotia. Can. J. Publ. Health-Rev. Can. San. 2001, 92, 331–334. [Google Scholar]
- World Health Organization. Rolling Revision of the WHO Guidelines for Drinking-water Quality: Nitrates and Nitrates in Drinking-water. 2004. Available online: http://www.who.int/water_sanitation_health/dwq/chemicals/en/nitrateschap1.pdf (accessed on 2 October 2007). [Google Scholar]
- Health Canada. Nitrate/Nitrite. 1992. Available online: http://www.hc-sc.gc.ca/ewh-semt/pubs/water-eau/doc_sup-appui/nitrate_nitrite/index_e.html#Guideline (accessed on 26 January 2006). [Google Scholar]
- Fields, S. Global nitrogen: Cycling out of control. Environ. Health Perspect. 2004, 112, 557–563. [Google Scholar]
- Bruning-Fann, C.S.; Kaneene, J.B. The effects of nitrate, nitrite and N-nitroso compounds on human health: A review. Vet. Hum. Toxicol. 1993, 35, 521–538. [Google Scholar]
- Fan, A.M.; Willhite, C.C.; Book, S.A. Evaluation of the nitrate drinking water standard with reference to infant methemoglobinemia and potential reproductive toxicity. Regul. Toxicol. Pharmacol. 1987, 7, 135–148. [Google Scholar] [CrossRef]
- Givelber, H.M.; DiPaolo, J.A. Teratogenic effects of N-Ethyl-N-nitrosourea in the syrian hamster. Cancer Res. 1969, 29, 1151–1155. [Google Scholar]
- Inouye, M.; Murakami, U. Teratogenic effect of N-Methyl-N'-nitrosoguanidine in mice. Teratology 1978, 18, 263–268. [Google Scholar] [CrossRef]
- Koyama, T.; Handa, J.; Handa, H.; Matsumoto, S. Methylnitrosourea-induced malformations of brain in SD-JCL rat. Arch. Neurol. 1970, 22, 342–343. [Google Scholar] [CrossRef]
- Dorsch, M.M.; Scragg, R.K.; McMichael, A.J.; Baghurst, P.A.; Dyer, K.F. Congenital malformations and maternal drinking water supply in rural South Australia: A case-control study. Amer. J. Epidemiol. 1984, 119, 473–486. [Google Scholar]
- Arbuckle, T.E.; Sherman, G.J.; Corey, P.N.; Walters, D.; Lo, B. Water nitrates and CNS birth defects: A population-based case-control study. Arch. Environ. Health 1988, 43, 162–167. [Google Scholar] [CrossRef]
- Croen, L.A.; Todoroff, K.; Shaw, G.M. Maternal exposure to nitrate from drinking water and diet and risk for neural tube defects. Amer. J. Epidemiol. 2001, 153, 325–331. [Google Scholar] [CrossRef]
- Cedergren, M.I.; Selbing, A.J.; Lofman, O.; Kallen, B.J. Chlorination byproducts and nitrate in drinking water and risk for congenital cardiac defects. Environ. Res. 2002, 89, 124–130. [Google Scholar] [CrossRef]
- Manassaram, D.M.; Backer, L.C.; Moll, D.M. A review of nitrates in drinking water: Maternal exposure and adverse reproductive and developmental outcomes. Environ. Health Perspect. 2006, 114, 320–327. [Google Scholar] [CrossRef]
- Trescott, P.C. Groundwater Resources and Hydrogeology of the Annapolis-Cornwallis Valley, Nova Scotia; Halifax: Nova Scotia, AB, Canada, 1968. [Google Scholar]
- Rivard, C.; Deblonde, C.; Boivin, R.; Boldue, A.; Paradis, S.J.; Liao, S.; Gauthier, M-J.; Blackmore, A.; Trepanier, S.; Castonguay, S.; et al. Canadian Groundwater Inventory: Hydrogeological Atlas of the Annapolis Valley, Nova Scotia. Geological Service of Canada: Ottawa, ON, Canada, 2007. [Google Scholar]
- The Municipality of the County of Kings. Water Utility. 2005. Available online: http://www.county.kings.ns.ca/engpw/watutil.htm (accessed on 13 July 2006). [Google Scholar]
- Wolfville Water Utility. Public Information Brochure. 2002. Available online: http://www.town.wolfville.ns.ca/forms/waterbrochurejan2002.pdf (accessed on 17 April 2006). [Google Scholar]
- The Town of Kentville. Kentville Water Commission. 2006. Available online: http://www.town.kentville.ns.ca/water.pdf (accessed on 12 July 2006). [Google Scholar]
- The Town of Port Williams. Nova Scotia Port Williams Industrial Park. 2004. Available online: http://www.targetnovascotia.com/IPPDF/PortWilliams.pdf (accessed on 12 July 2006). [Google Scholar]
- Province of Nova Scotia. Nova Scotia Civic Address File (NSCAF). 2008. Available online: http://www.gov.ns.ca/snsmr/land/projects/civic/ (accessed on 15 April 2008). [Google Scholar]
- Benson, V.S.; VanLeeuwen, J.A.; Sanchez, J.; Dohoo, I.R.; Somers, G.H. Spatial analysis of land use impact on ground water nitrate concentrations. J. Environ. Qual. 2006, 35, 421–432. [Google Scholar] [CrossRef]
- Ruckart, P.Z.; Henderson, A.K.; Black, M.L.; Flanders, W.D. Are nitrate levels in groundwater stable over time? J. Expo. Sci. Environ. Epidemiol. 2008, 18, 129–133. [Google Scholar]
- Briggins, D.R.; Moerman, D.E. Pesticides, nitrate-N and bacteria in farm wells of King’s County, Nova Scotia. Water Qual. Res. J. Can. 1995, 30, 429–442. [Google Scholar]
- Aller, L.; Bennett, T.; Lehr, J.H.; Petty, R.J.; Hackett, G. DRASTIC: A Standardized System for Evaluating Ground Water Pollution Potential using Hydrogeologic Settings; EPA: Ada, OK, USA, 1987. [Google Scholar]
- Levallois, P.; Theriault, M.; Rouffignat, J.; Tessier, S.; Landry, R.; Ayotte, P.; Girard, M.; Gauvin, D.; Gingras, S.; Chiasson, C. Groundwater contamination by nitrates associated with intensive potato culture in Quebec. Sci. Total Envir. 1998, 217, 91–101. [Google Scholar] [CrossRef]
- Rudolph, D.L.; Barry, D.A.J.; Goss, M.J. Contamination in Ontario farmstead domestic wells and its association with agriculture: Results from multilevel monitoring well installations. J. Contam. Hydrol. 1998, 32, 295–311. [Google Scholar] [CrossRef]
- Woods, S.E.; Raju, U. Maternal smoking and the risk of congenital birth defects: A cohort study. J. Am. Board Fam. Med. 2001, 14, 330–334. [Google Scholar]
- Morales-Suarez-Varela, M.; Bille, C.; Christensen, K.; Olsen, J. Smoking habits, nicotine use, and congenital malformations. Obstet. Gynecol. 2006, 107, 51–57. [Google Scholar] [CrossRef]
- Malloy, M.H.; Kleinman, J.C.; Bakewell, J.M.; Schramm, W.F.; Land, G.H. Maternal smoking during pregnancy: No association with congenital malformations in Missouri 1980–1983. Amer. J. Public Health 1989, 79, 1243–1246. [Google Scholar] [CrossRef]
- Carmichael, S.L.; Shaw, G.M.; Laurent, C.; Olney, R.S.; Lammer, E.J. Maternal reproductive and demographic characteristics as risk factors for hypospadias. Paediatr. Perinat. Epidemiol. 2007, 21, 210–218. [Google Scholar] [CrossRef]
- Akre, O.; Lipworth, L.; Cnattingius, S.; Sparen, P.; Ekbom, A. Risk factor patterns for cryptorchidism and hypospadias. Epidemiology 1999, 10, 364–369. [Google Scholar] [CrossRef]
- Persad, V.L.; van den Hof, M.C.; Dube, J.M.; Zimmer, P. Incidence of open neural tube defects in Nova Scotia after folic acid fortification. Can. Med. Assn. J. 2002, 167, 241–245. [Google Scholar]
- Ericson, A.; Kallen, B.; Lofkvist, E. Environmental factors in the etiology of neural tube defects: A negative study. Environ. Res. 1988, 45, 38–47. [Google Scholar] [CrossRef]
- Mattix, K.D.; Winchester, P.D.; Scherer, L.R. Incidence of abdominal wall defects is related to surface water atrazine and nitrate levels. J. Pediat. Surg. 2007, 42, 947–949. [Google Scholar] [CrossRef]
- Brender, J.D.; Olive, J.M.; Felkner, M.; Suarez, L.; Marckwardt, W.; Hendricks, K.A. Dietary nitrites and nitrates, nitrosatable drugs, and neural tube defects. Epidemiology 2004, 15, 330–336. [Google Scholar] [CrossRef]
- Moerman, D.; Briggins, D. Nova Scotia Farm Well Water Quality Assurance Study Final Report; Province of Nova Scotia: Halifax, NS, Canada, 1994.
- Blair, K. Temporal and Spatial Profiles of Groundwater Nitrate Concentration in Kings County, Nova Scotia. Master Thesis, Dalhousie University, Halifax, NS, Canada, 2001. [Google Scholar]
- Nuckols, J.R.; Ward, M.H.; Jarup, L. Using geographic information systems for exposure assessment in environmental epidemiology studies. Environ. Health Perspect. 2004, 112, 1007–1015. [Google Scholar]
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