Parasitic worms of the genus Schistosoma inhabit the urogenital or the intestinal tract of the human host, with parasite eggs excreted in human urine and feces, respectively. Freshwater snails of the genera Bulinus serve as the intermediate host of S. haematobium while Biomphalaria transmit S. mansoni. These snail genera have distinct ecologies: Bulinus snails are able to withstand prolonged periods of drying while Biomphalaria are sensitive to saline conditions. Species from both genera, however, can colonize irrigation canals. Expansion of snail habitat and increased human activity in the aquatic environment both increase transmission in dammed and irrigated areas. However, few studies disentangle the environmental and socio-behavioral mechanisms of schistosomiasis occurrence in areas where water resources are actively managed. Of the approximately 800 million people at risk for schistosomiasis worldwide, 100 million live in close proximity to dams and irrigation schemes. An estimated 200 million are infected, the majority of which live in sub-Saharan Africa. Parasites exiting snail hosts penetrate the skin of people who are in direct contact with water. Acute symptoms of schistosomiasis include hematuria for S. haematobium infection and diarrhea and abdominal pain for S. mansoni infection. Prolonged infection can lead to anemia, organ damage, and cancer. While lethal pathologies are linked to infection with both S. haematobium and S. mansoni, deaths are not often officially attributed to infection, and as a result, are likely underestimated. Because available treatments do not prevent re-infection, regular contact with water can lead to chronic infection and severe disease. In some settings, prevalence and intensity of infection remain high even in the presence of treatment programs. Existing evidence linking irrigated agriculture and schistosome infection relies on village- or landscape-level aggregations of disease occurrence and agricultural activity ,plastic pots plants but finer-scale processes associated with irrigation influence exposure to parasites present in surface water.

The household is a particularly relevant unit for both agricultural activity and water contact behavior. However, few studies investigate whether household-level circumstances compound infection risk present in the environment. In this study, we investigated whether participation in agriculture at the household level was associated with individual-level schistosome infection. We assumed that in rural areas, the majority of schistosome exposure would occur at water access sites within a village and hypothesized that household-level cultivation of irrigated crops may represent additional exposure beyond the village-based exposure that occurs for most people. As a result, we suspected that children living households that cultivated irrigated land would be more likely to be infected with both species of schistosome. We further reasoned that, because larger areas of irrigated land are served by greater lengths of irrigation infrastructure, the occurrence of schistosomiasis would further increase in households that were cultivating larger areas of land. Larger fields served by more irrigation infrastructure would require more person-time to manage, harbor more snails, produce more parasites and, ultimately, increase schistosome exposure. With this rationale, we examined the relationship between area of irrigated land reported at the household level and individual-level infection outcomes, focusing on school-aged children who are often the target of mass drug administration campaigns. While studies of both schistosomiasis ecology and water contact behavior often focus on the water access sites within a village, human contact with agricultural water sources could play an important role in sustaining schistosome transmission in a way that threatens the success of ongoing schistosomiasis control efforts. While the spatial distribution of agricultural water sources makes them difficult to monitor, processes of exposure and contamination in agricultural water sources may contribute to the contamination of village water sources and lead to re-infection after treatment. Such processes may contribute to the development of persistent hot spots of schistosomiasis transmission. For schistosome transmission to be successfully suppressed, the implementation of interventions needs to account for the spatial scale of all the transmission sites in and around a village and the human movement between them. Te lower basin of the Senegal River became hyperendemic for schistosome transmission following the construction of the Diama dam in 1986, which was designed as a saltwater barrier to support agricultural development.

Prior to dam construction, S. haematobium infections occurred seasonally at low levels, while S. mansoni was absent from the region. By preventing saltwater intrusion, stabilizing water levels, promoting vegetation growth and disrupting the life histories of snail predators, the dam triggered environmental changes that favored the snail-borne transmission cycles of both S. haematobium and S. mansoni. Salt-sensitive Biomphalaria have since become established in the perennially freshwater environment, while the irrigation infrastructure provides new habitat for both Bulinus and Biomphalaria. The prevalence and intensity of both infections remain high today in human populations, and agricultural practices have increasingly shifted to the cultivation of irrigated crops. Given the environmental changes affecting both parasite transmission and livelihoods in this setting, we aimed to understand whether household engagement in irrigated agriculture compounds the infection risk created by the dam, and whether agricultural sites of water contact may be involved in schistosome transmission in this setting. Specifically, we investigated whether schistosome infection increased in school-aged children living.This is study used cross-sectional data collected as part of a longitudinal study of schistosome infection in school aged children and the socio-economic conditions of the households where those children resided. Sixteen villages along the Senegal River, its tributaries and the Lac de Guiers in northwest Senegal were chosen to represent rural, high-transmission sites common in the region . Village selection criteria are described in detail elsewhere, but included proximity to freshwater and presence of water access sites, presence of a school with sufficient enrollment in target grades and a non-zero prevalence of self-reported infection as well as accessibility in the rainy season. School-aged children were recruited from grades 1–3 in village schools. Agriculture was common in all villages with cultivation of irrigated rice using constructed irrigation infrastructure undertaken primarily in river villages and gardening and monocropping supported by hand-dug infrastructure in lake villages.Parasitological data were derived from a single year of a longitudinal, school-based parasitological study in all 16 villages.

A total of 1480 school-aged children were enrolled at baseline in February–April 2016. Of those, 1479 remained enrolled in January–April 2017 and 1414 successfully produced urine or stool samples on the two testing days that year . On each testing day, one urine and one stool sample were collected from each child enrolled in the study. Urine and stool sample collection was organized at the school by trained personnel from the Biomedical Research Center Espoir Pour La Sante. Sampling pots were provided to each participant 24 h in advance, and samples were kept in isothermal boxes during transport back to the laboratory. Samples were analyzed by urine fltration for S. haematobium infection and duplicate Kato-Katz examination of stool samples for S. mansoni infection by standard methods. In each year of the longitudinal study, all children were treated with 40 mg/kg of praziquantel following sample collection. The cross-sectional parasitological data from 2017 data used in this study, thus, refect post-treatment re-infection over the preceding year.Household survey were data collected in August 2016, during the rainy season preceding the 2017 parasitology data collection. We aimed to reach all the households where school-aged children enrolled in the parasitology study resided. The household survey instrument included six modules . The modules used in this analysis included demographic and occupational information for every member of the household,plastic nursery pots agricultural land use for all parcels owned and/or cultivated by household members, and data on building materials and durable assets, which were used to approximate socio-economic status. Surveys were completed in 655 households . The questionnaire was developed in English and translated to French by native speaking members of the field team. A team of eight Senegalese enumerators were trained to obtain verbal informed consent, pose survey questions in Wolof and record data in French. Prior to data collection, all survey questions were reviewed in French and the proper Wolof translations of key terms and ideas were discussed at length and agreed upon by all members of the enumerator team.We find evidence that the occurrence of S. haematobium but not S. mansoni infections in a dammed landscape is compounded by engagement in agricultural livelihoods. In the lower basin of the Senegal River, the presence of S. haematobium infections in school-aged children increase with irrigated area cultivated by members of their households. This may result from greater contact with Bulinusand S. haematobium-laden water among children whose families use and manage infrastructure for irrigating crops, compared to those whose contact occurs primarily at village water access sites. The observed association between irrigated area on S. mansoni infection presence was smaller and more uncertain, as were the associations of irrigated area with both measures of infection intensity, preventing frm conclusions about these outcomes. The contrast between S. haematobium and S. mansoni outcomes may reflect different sources of contamination in agricultural surface waters, such that the circulation of S. haematobium is more easily sustained by the input of urine than S. mansoni by the input of feces.

Our use of individual- and household-level data suggest that irrigated agriculture contributes to increased infection risk beyond the environmental consequences of infrastructure development. Previous meta-analysis on the topic revealed a greater increase in the occurrence of S. mansoni compared to S. haematobium in irrigated areas at the landscape scale. This and other studies that have examined landscape-scale measures of disease occurrence and land use support the notion that human-mediated environmental change is associated with elevated infection prevalence, but do not shed light on the finer-scale mechanisms that influence individual infection risk. The relationship between disease risk and environmental exposures depends on the scales at which the relevant biotic, abiotic and human factors operate, such that individual- and landscape level processes of disease and land use are not interchangeable and may represent distinct constructs. In the lower basin of the Senegal River, dam construction in support of agricultural development has altered the landscape by stabilizing water levels, preventing saltwater intrusion and expanding the aquatic habitat available to the snails that transmit schistosomes. Our use of finer-scale data establishes that processes related to household land use also play a role in determining risk for acquiring infection from the environment.These findings also suggest that—beyond the in-village water access sites that are the typical focus of studies of schistosome ecology and water contact behavior—agricultural water sources play a role in sustaining schistosome transmission and connecting transmission sites to each other. Te frequent use of irrigation canals for a wide variety of activities is likely to result in both snail-to human and human-to-snail transmission in water sources outside a village. This may be particular true for S. haematobium, whose eggs can be introduced more easily into the environment through urination compared to S. mansoni, whose eggs get introduced into the environment through defecation. If exposure and contamination occurs in both village and agricultural water sources, the human movement and water contact behaviors that connect these water sources will inevitably expand the spatial scope of transmission and the interventions needed to interrupt it. Networks of water sources may ensure continuous introduction of parasites into a village, perpetuating transmission, threatening the success of both MDA and environmental interventions and potentially leading to the formation of persistent hot spots. In this way, the design of interventions must account for the influence of human behavior on the ecological processes that affect infection risk at the proper scales. As calls continue for environmental interventions to complement mass drug administration, the development of implementation guidelines should consider for the full spectrum of water contact activity and the disperse water sources that might contribute to transmission in a particular setting. The ability of water, sanitation and hygiene interventions to reduce both exposure- and contamination-related behaviors, for example, may not be effective if agricultural water sources are disregarded. Environmental complements to MDA interventions may include cleaning aquatic vegetation to reduce snail habitat and chemical and biological control of snail populations in both water access points and irrigation canals. This research has some limitations. Odds only approximate risk when outcomes are rare. Because the outcomes in this study are not rare, our estimates are biased away from the null compared to prevalence ratios. We attempted to directly estimate prevalence ratios by fitting log-binomial models, but these models did not converge.