Preliminary Study of Pesticide Drift into the Maya Mountain Protected Areas of Belize
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- Kaiser, K. Bull Environ Contam Toxicol (2011) 86: 56. doi:10.1007/s00128-010-0167-x
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In Belize, Central America, many farms surrounding the Protected Areas of the Maya Mountains rely heavily on the application of agrochemicals. The purpose of this study was to test whether orographic drift of glyphosate and organophosphates into the nearby Maya Mountain Protected Areas occurred by collecting phytotelmic water from seven sites over 3 years. Regardless of location within the Maya Mountain Protected Areas, glyphosate was present; organophosphates were more common at ridge sites. Although glyphosate concentrations were low, due to the number of threatened species and the human use of stream water outside the Maya Mountain Protected Areas, better understanding of these effects is warranted.
KeywordsGlyphosate Organophosphates Orographic precipitation
Globally, the use of pesticides and herbicides has become commonplace. Chemicals are often applied by spray (e.g., from backpacks or airplanes), where aerosol can be dispersed by wind or overspray can runoff into aquatic ecosystems. The use of these chemicals and their overspray has given rise to a multitude of studies of the toxicological effects of pesticides on non-target species, as well as the impact of pesticide drift into freshwater ecosystems (reviewed by Relyea and Hoverman 2006).
The purpose of this study was to test the hypothesis that pesticides applied to areas surrounding the Maya Mountain Protected Areas of Belize would be carried into the protected areas, maximally impacting regions immediately bordered by agricultural lands and cloud forests on the eastern edge of the Maya Mountains. If this were the case, orographic precipitation would cause the majority of toxicants to fall on the outer ridges of the Maya Mountains, and the central plateau would be relatively less impacted by agrochemicals from regions surrounding protected areas.
Materials and Methods
A total of seven sites across the protected areas of the Maya Mountains were sampled during June–August, 2006–2007 (Fig. 1), the rainiest months of the year in this region. Based on self-reported use of agrochemicals (Banana Growers Association, pers. comm.) and Citrus Growers Association (Nunny et al. 2001), glyphosate and common organophosphates and carbamate (OP/C) tests were implemented.
Results of glyphosate and OP/C tests
Mean [glyphosate] (μg/L)b
N positive OP/C
Range of sensitivity of organophospate/carbamate kit
Minimum sensitivity (μg/L)
Maximum sensitivity (μg/L)
All tests were conducted according to kit instructions, and using the provided reagents. Briefly, for OP/C tests, 100 μL of sample were incubated at approximately 20°C for 5 min with oxider, neutralized, incubated for 30 min at 20°C with lyophilized actylcholinesterase. Acetylthiocholine and 5,5′-Dithio-bis(2-Nitrobenzoic Acid) were then added, and the reaction stopped. For glyphosate tests, 50 μL of anti-glyphosate antibody was combined with 50 μL of sample and incubated for 30 min; 50 μL of enzyme conjugate solution was then added and samples incubated for a further 60 min. Sample wells were then washed, and 150 μL of color solution added to wells. After 30 min of incubation, the reaction was stopped. For both OP/C and glyphosate, absorbance at 450 nm was read immediately after stopping reactions. No attempt to concentrate samples was made.
Glyphosate ELISA reaction gave absolute quantification; the OP/C kit tested for presence of any chemical in this family. Samples for all tests were run in duplicate. Statistical analysis was carried out using StataIC 10.0 (StataCorp, College Station, TX).
Results and Discussion
Glyphosate was detected at all sites sampled (Table 1). Organophosphates/carbamate were detected at all sites, but the non-specificity of the kit makes it impossible to determine either the specific chemical present in the sample or its absolute concentration (Table 1). Glyphosate values in one sample from one site tested above the maximum quantifiable concentration of the kit (5 μg/L). A conservative estimate of 5 μg/L was used for statistical purposes; the duplicate of this sample tested within the range of the test kit. For samples which tested positive in duplicate, the average of the two concentrations for all statistical tests was used. For samples which tested positive only once, only the single value was used.
All plateau samples were taken in 2007, but ridge samples spanned the rainy seasons of 2006–2007. No significant differences were detected in concentration of glyphosate (t = −1.3224, df = 48, p = 0.192), proportion of samples positive for glyphosate (z = −0.2340, n1 = 30, n2 = 20, p = 0.815) or OP/C (z = 1.416, n1 = 28, n2 = 20, p = 0.157) among years. Samples were then pooled to compare Vaca Plateau and ridge sites. Sites on the Vaca Plateau did not have a significantly different concentration of glyphosate than did sites along the eastern ridges of the protected areas (t = 0.26, df = 64, p = 0.800; Fig. 1). The proportion of positive glyphosate samples at the ridge versus plateau sites did not differ (z = −0.7660, n1 = 50, n2 = 16, p = 0.444). Sites did differ in proportion positive for organophosphates, with no plateau samples testing positive for these chemicals (z = 3.698, n1 = 48, n2 = 16, p = 0.0002).
The observed differences in pesticide distribution can be interpreted in several different ways. The organophosphate/carbamate test is non-specific, and the minimum sensitivity for various chemicals varies widely (Table 1). It is possible that the OP/C present in plateau samples are simply present at concentrations lower than the ridge samples, and below the sensitivity of the test. Another explanation is that the detected OP/C were used not in commercial agricultural areas, but in villages surrounding protected areas, either on crops or as mosquito prophylaxis. OP/C pesticides have varying stability and half-life in water (Evert 2002; Newhart 2006; Xu 2000). Differences in samples may simply reflect differences in time since application of pesticides: glyphosate may simply have been applied more recently than was OP/C. Furthermore, glyphosate is stable to photodegradation (EPA 1993), while this is not the case for all organophosphates (e.g., Wolfe et al. 1978); care was taken to protect samples from light after collection, but it was impossible to control for the time between the most recent rainfall and the sample collection, as no weather data exist for these sites.
The ecological impact of such low concentrations of glyphosate being carried into protected areas is unclear. Studies have shown that glyphosate exhibits low toxicity to fish and aquatic invertebrates (Folmar et al. 1979; Giesy et al. 2000; Neškovi et al. 1996), but the effects of glyphosate vary widely based on formulation (Mann and Bidwell 1999; Tsui and Chu 2003). Although some preparations contain surfactants that significantly depress the LC50, requiring these products to be labeled as toxic to fish (EPA 1993), even these decreased toxic levels are in the 1.4–18 mg/kg range (LC5024h), and thus above the levels found in this study (Folmar et al. 1979). However, there is growing evidence that sublethal concentrations of pesticides may affect a variety of behavioral and physiological responses (reviewed in Weis et al. 2001).
Also important to consider is the downstream effect of pesticide drift. Only a subset of the commonly used chemicals were tested. In Belize, municipal water exists only in portions of the country, and at least part of the population gets its drinking water from stream water coming from the Maya Mountain Protected Areas (Aimpun and Hshieh 2004). People in surrounding villages also use streams for bathing, swimming, and watering livestock. Thus, a monitoring program for stream water in the communities surrounding the farms near the protected areas would allow researchers to determine the safety of such water.
The results of this study suggest that pesticide drift is occurring, with no difference among years in sample detection. The effect of this drift on the fauna of the Maya Mountain Protected Areas is unknown, but a greater understanding of how species respond to pesticides may be one of the most pressing conservation questions, as well as how these residues affect pesticide concentrations downriver at the level of villages, where water may be used by humans.
D.P. Janos and D. Kremples provided equipment for analyses. Funding was provided by the Columbus Zoo and Aquarium and the Critical Ecosystems Partnership Fund. Wildtracks provided infrastructure. P. Edgar, N. Mora, and E. Garcia provided field assistance. P.M. Narins and an anonymous reviewer provided helpful feedback on an earlier version of the manuscript.
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