Leptospira in river and soil in a highly endemic area of Ecuador
BMC Microbiology volume 21, Article number: 17 (2021)
Leptospira are shed into the environment via urine of infected animals. Rivers are thought to be an important risk factor for transmission to humans, though much is unknown about the types of environment or characteristics that favor survival. To address this, we screened for Leptospira DNA in two rivers in rural Ecuador where Leptospirosis is endemic.
We collected 112 longitudinal samples and recorded pH, temperature, river depth, precipitation, and dissolved oxygen. We also performed a series of three experiments designed to provide insight into Leptospira presence in the soil. In the first soil experiment, we characterized prevalence and co-occurrence of Leptospira with other bacterial taxa in the soil at dispersed sites along the rivers (n = 64). In the second soil experiment, we collected 24 river samples and 48 soil samples at three points along eight transects to compare the likelihood of finding Leptospira in the river and on the shore at different distances from the river. In a third experiment, we tested whether Leptospira presence is associated with soil moisture by collecting 25 soil samples from two different sites.
In our river experiment, we found pathogenic Leptospira in only 4 (3.7%) of samples. In contrast, pathogenic Leptospira species were found in 22% of shore soil at dispersed sites, 16.7% of soil samples (compared to 4.2% of river samples) in the transects, and 40% of soil samples to test for associations with soil moisture.
Our data are limited to two sites in a highly endemic area, but the scarcity of Leptospira DNA in the river is not consistent with the widespread contention of the importance of river water for leptospirosis transmission. While Leptospira may be shed directly into the river, onto the shores, or washed into the river from more remote sites, massive dilution and limited persistence in rivers may reduce the environmental load and therefore, the epidemiological significance of such sources. It is also possible that transmission may occur more frequently on shores where people are liable to be barefoot. Molecular studies that further explore the role of rivers and water bodies in the epidemiology of leptospirosis are needed.
With over one million cases estimated yearly, leptospirosis is among the world’s most common zoonoses with a mean case fatality ratio of 6.85% . Pathogenic spirochaete species of the genus Leptospira have been detected in many geographic regions, but pose an especially prevalent threat in tropical and subtropical areas with poor sanitation infrastructure and increased exposure to infected wild, peri-domestic, and domestic animals [1,2,3,4].
The epidemiology of leptospirosis and ecology of Leptospira is particularly complex given the genetic diversity in the genus Leptospira. There are currently 64 species in the genus divided into two phylogenetic clades: 1) The “Saprophytic” clade contains species isolated from the environment that are not known to cause disease in humans and animals, and 2) the “Pathogenic” clade which includes species responsible for causing infections as well as species isolated from the environment with unknown virulence .
Survival of pathogenic Leptospira in the environment, after being shed in the urine of an infected animal, is critical for transmission to another host. Many human cases have been statistically attributed to river or lake exposure, suggesting high survival in larger bodies of water, however causal evidence is lacking and pathogenic leptospires have rarely been detected in these environments [6,7,8,9,10,11,12,13,14,15,16,17,18,19,20,21]. The soils bordering rivers may serve as a reservoir for these bacteria or otherwise reflect the presence of leptospires in rivers. Indeed, soil contamination has long been suspected as a possible source of Leptospira transmission and has received recent attention [22,23,24,25]. Given the perceived epidemiological importance of rivers, investigating the presence and survival of leptospires in river water and soil bordering rivers may better define where and how transmission in a riverine environment occurs.
Warm, humid climates and soil/water conditions are thought to be conducive to longer environmental survival times [3, 26]. Factors like high rainfall [27, 28], a neutral or slightly alkaline pH [6, 9, 11, 29], sediments in water [30, 31], low levels of human fecal contamination [30, 32], and high moisture in soil [9, 33] have been associated with the presence of Leptospira. Microbial communities in water and soil may also impact survival or indicate the presence of Leptospira. While different species of Leptospira may exhibit differential survival under different conditions, the extent of replication in the environment is largely unknown [34,35,36], despite the clear epidemiological importance of such knowledge. However, recent work with L. interrogans shows no replication in tested environmental microcosms, suggesting that the environment is only a temporary reservoir for this pathogen [22, 23]. In general, the roles and relative importance of environmental variables on Leptospira persistence are poorly understood, hindering the prediction of outbreaks.
We sought to investigate the presence of Leptospira in river water and soils from two highly endemic rural communities in Ecuador. In the towns of Calderón and Santa Ana, people and animals are dependent on nearby rivers for watering animals, drinking water, bathing, laundry, and transportation. Moreover, over the course of this study, leptospirosis cases were common in the community and we detected pathogenic Leptospira in both humans and animals . We therefore hypothesized that we would readily detect pathogenic Leptospira in samples collected in these riverine environments.
This study is part of a broader research project on the prevalence of pathogenic Leptospira in humans and animal reservoir in the communities of Abdon Calderon (1°2′25″S, 80°22′15″W), and Santa Ana de Vuelta Larga (1°12′25″S 80°22′15″W) . The two low-income, rural towns of Abdon Calderón (Site 1) and Santa Ana de Vuelta Larga (Site 2) are located near the coast in the Ecuadorian province of Manabí and approximately 20 km apart (S1 file). Prevalence of leptospirosis is high in this area with an average of ~ 448 human cases/year, higher than elsewhere in Ecuador (Barragan et al. unpublished). In these communities, multiple Leptospira species circulate among humans, cows, pigs, and rats . Unlike urban communities where rats are thought to be the main source of leptospirosis, in these rural communities, the prevalence in rats is low (~ 3%) compared to livestock (~ 33%) and probably impacts the ecology and epidemiology of this disease . Livestock and human interactions with the local rivers may be especially important as rivers are an established risk factor for leptospirosis .
The Chico River runs through Site 1 and the Portoviejo River runs through Site 2.
In order to explore the presence of pathogenic Leptospira in river water and soil samples, we used four different sampling strategies: 1) From each of these two rivers, we collected samples from sites upstream and downstream of the towns (described below in River Experiment). 2) From multiple sites along the shore of each river, we collected soil samples (described in Soil Experiment #1). 3) We intensively sampled soil from two sites, across a water-shore transect (Soil Experiment #2), and 4) intensively sampled soil at two locations to determine associations with soil moisture (Soil Experiment #3). All river collection sites are commonly used by the local population for swimming and watering their livestock (cattle, sheep and goats).
River experiment – Leptospira prevalence and abiotic associations
River water samples were collected between December of 2013 and March of 2015 (see Fig. 1 for sample collection timeline). When possible, sampling was performed in monthly intervals. For sites 1 and 2, the downstream sampling locations were ~ 1.6 km and 1.2 km (respectively) downriver from the upstream locations. At each time point, we collected 2 water samples (40 mL each) from the main current (not from near the shore) at both upstream and downstream sites in each river for a total of 14 time points and 112 river water samples (Fig. 1). All samples were immediately stored at 4 °C for transport and subsequently at − 20 °C until DNA extraction.
For each river, we used a GL500U-2-1 water sensor (Global Water, Gold River, CA) to log river depth on an hourly basis between February of 2014 and June of 2015. We also collected pH, dissolved oxygen (mg/L), and temperature (°C) of river water concurrent with sample collection, between July of 2014 and March of 2015.
Soil experiment #1 - Leptospira prevalence and co-occurrence with other bacteria
We collected surface soil samples (no more than 3 cm in depth) from multiple sites along the shores of both rivers in July (n = 38) and August (n = 26) of 2014. Soil samples were collected on the shore 5 m from the river edge.
Soil experiment #2 - Leptospira prevalence along water-shore transects
In April and May of 2015, we collected samples along eight transects next to the Chico (4 transects) and Portoviejo Rivers (4 transects) (Fig. 2). Samples from each transect were collected at the same time point. Each transect had three sampling points: 1) water collected 1.5 m from the shore, 2) on the shore immediately next to the river, and 3) on the shore 1.5 m from the river. For the 2nd and 3rd positions in each transect, we collected the upper 5 mm of soil. For the 1st sampling positions, we collected 40 mL of river water as described above in our River Experiment. All samples were collected in triplicate for a total of 9 samples from each transect and 72 total samples. After collection, all samples were immediately stored at 4 °C for transportation and subsequently at − 20 °C until DNA extraction .
Soil experiment #3 - Leptospira association with soil moisture content
In July 2018, we collected 25 soil samples at two sites within 1.5 m from the shore of the Chico River at the same location as the river sampling and two of the transect sites (Ecuadorian permits: MAE-DNB-CM-2018-0085 and MAE-CGZ4-DPAM-2018-1457-O). For each sample, approximately 150 g of soil was collected in a sterile ziplock bag and immediately stored at 4 °C for transportation: 100 g of soil was used for measuring soil water content (moisture). The weight of the sample was measured before and after drying with a Drier Box DHG-9030A at 105 °C for 24 h to determine the water content . Samples DNA extraction was performed as described below, and tested using the SNP111 assay to detect infectious Leptospira .
DNA from individual soil samples was extracted using the PowerSoil® DNA Isolation Kit (MO BIO, Carlsbad, CA, USA), while DNA from river water samples was extracted using the PowerWater® DNA Isolation Kit (MO BIO, Carlsbad, CA, USA). DNA extraction from soil and water samples was performed in duplicate and triplicate, respectively. The manufacturer’s protocols were followed with the exception of the final elution into 2 mL tubes using 100 uL of Buffer AE (Qiagen, Valencia, CA, US), as opposed to Solutions C6 for soil and PW6 for water. This alteration was made due to the stabilizing effect of the EDTA content of Buffer AE’s composition (10 mM Tris-Cl; 0.5 mM EDTA, pH 9.0).
Detection of infectious and saprophytic Leptospira
DNA extractions were then screened using the SNP111 TaqMan qPCR assay to detect members of the pathogenic and intermediate Leptospira clades , also referred to as P1 and P2 clades . To detect the presence of member of the saprophytic Leptospira clade, also referred to as S1 file , we designed the Sapro assay, a single TaqMan® MGB probe assay (S1 file). All PCR assays were performed in quadruplicate.
As a quality control for PCR, we sought to determine the extent to which our PCR was being inhibited, either by humic acids or excessive amounts of extracted DNA. 10% of samples from each sample type (e.g., water, soil) were randomly selected for inhibition testing. Each sample was divided into two aliquots: one was used as a control, and the other was spiked with Leptospira DNA such that it contained 1 μL of sample extraction template plus 1 μL of the positive control plasmid. Both aliquots were tested with the SNP111 Assay. The presence of inhibitors in a sample would be indicated by a diminished amplification of the 153 bp positive control target band. Samples did not show inhibition.
16S community sequencing
We investigated the microbial community structure for a subset of samples collected in Soil Experiment #1 (n = 59 out of 64). Samples were indexed and prepared for sequencing according to the 16S rRNA Amplification Protocol of the Earth Microbiome Project . All PCR products were cleaned with carboxylated magnetic beads, both before and after pooling. Upon observing an acceptable quantity and purity of the pooled samples, a quantitative PCR using Illumina DNA Standards was carried out to verify overall target DNA concentrations (Kapa Biosystems, Wilmington, MA). Samples were all sequenced on MiSeq Desktop Sequencers (Illumina Inc., San Diego, CA) using MiSeq Reagent Kits v2 at a read length of 2 × 150.
Sequence data returned by each MiSeq run was processed using QIIME 22019.7 . Sequence quality control and definition of amplicon sequence variants (ASVs) was performed with DADA2  using the q2-dada2 QIIME 2 plugin. Sequences were processed with and without paired end read joining, and ultimately we chose to proceed with analysis of unpaired forward reads as read joining resulted in loss of approximately 50% of sequences. After definition of ASVs, sample replicates were collapsed by the site they were derived from by summing ASV counts across replicates. The Observed OTUs (OO), Faith’s Phylogenetic Diversity , unweighted UniFrac, and weighted UniFrac diversity metrics  were computed out using an even sampling (rarefaction) depth of 7164 sequences per sample. Taxonomy was assigned to ASV sequences using the q2-feature-classifier , Naïve Bayes classifier  and the Greengenes 13_8 reference database . A phylogenetic tree was constructed using q2-fragment-insertion . We next tested for differences in community composition (beta diversity) and community richness (alpha diversity), and for differentially abundant ASVs and genera across samples which had any positive Leptospira hits and those sites that didn’t have any positive Leptospira hits. Kruskal-Wallis was applied to test for differences in community richness, PERMANOVA for community composition, and ANCOM  for differentially abundant ASVs and genera.
To test the effects of environmental covariates on the presence of Leptospira in river water, we conducted a logistic regression with a quasibinomial error distribution to account for under-dispersion in the data (dispersion parameter estimated as 0.75). We considered a sample to be positive if any of the two qPCR tests (SNP111 and Sapro assays) were positive, thus including members of the pathogenic, intermediate, and saprophytic Leptospira clades (see qPCR methods described above). We combined pathogenic, intermediate, and saprophytic Leptospira to increase the number of positive samples and because the shared evolutionary history of these Leptospira are likely to lead to shared ecological qualities. As such, environmental covariates for one type may shed light on others, independent of whether they cause disease in humans. We started with a full model that included the effects of total monthly precipitation, river depth, dissolved oxygen, pH, water temperature, and a fixed effect of river identity. All continuous covariates were centered by subtracting the mean before analysis. We then used step-wise model selection to determine the most parsimonious model. We dropped variables sequentially and conducted a likelihood ratio test to determine whether dropping variables was appropriate, using an alpha value of 0.05 as our drop threshold. The final model included total monthly precipitation, depth, pH, and river identity. All analyses were conducted in the open-source statistical programming software, R .
Performance of the assay for detecting saprophytic Leptospira
The Sapro assay appears to be capable of detecting Leptospira species within the saprophytic clade. Extensive in silico analysis of 278 Leptospira 16S rRNA gene sequences that were publicly available at the time of assay design (July 2014) as well as 26 saprophytic species suggests that the Sapro assay is specific for species within the saprophytic clade (S1 file). The probe and forward primer bind perfectly to all 26 saprophytic species while the reverse primer contains a single mismatch with 2/26 species (S1 file). Also, laboratory tests showed that none of the infectious Leptospira species, or the 10 non-Leptospira species amplified with the assay (S1 file). However, Leptonema illini synthetic DNA was amplified by this assay, suggesting the possibility for false positive results. The Sapro assay exhibited a lowest limit of quantification (LoQ) and lowest limit of detection (LoD) to be ten 16S rRNA copies per microliter of extracted DNA in Qiagen AE elution buffer (S1 file). The range of linearity of the Sapro assay was 10^8 to10^1 16S rRNA genes.
River experiment – Leptospira prevalence and abiotic associations
We detected infectious Leptospira in four of 112 (3.6%) river water samples; however, only a very small amount of Leptospira DNA was present as all amplification curves appeared at very late cycles (average Ct of 35.7: range = 35–36.16). This average Ct corresponds to one 16S copy and is within the limit of detection of the SNP111 assay. We found evidence of saprophytic Leptospira in nine samples. As with our detection of infectious Leptospira, the Sapro assay suggests very small quantities of saprophytic DNA (average Ct of 35.96, corresponding to one 16S copy, Ct values ranged from 26.59–43.17). Unlike the SNP111 assay, Ct values above approximately 34 fall outside the limit of detection, indicating that saprophytic species are present at concentrations that are too low to produce reliable detection. While sampling took place from December of 2013 through March of 2015, Leptospira were nearly exclusively detected in wet months (Fig. 1).
We were more likely to detect Leptospira (saprophytic and infectious) when rivers were shallower and in months with higher total precipitation, and Leptospira was less likely to be found in water with high pH (Table 1, Fig. 1b). Although we found 7 positive samples in the Chico River (Site 1) and 6 positive samples in the Portoviejo River (Site 2), the model shows a higher likelihood of Leptospira presence in the Portoviejo River, after accounting for the other environmental covariates. This effect is likely due to the fact that, although Leptospira was more likely to be found when rivers were shallower, the Portoviejo River had on average higher depth compared to the Chico River (118.0 vs 90.0 cm, respectively). Therefore, to account for the positive samples found in the Portoviejo River at higher average depths, the model estimates an overall higher likelihood of detecting Leptospira in the Portoviejo River. Based on a separate logistic regression a priori, there was no difference in the proportion of positive samples detected upstream versus downstream (z = 1.439, p = 0.15). Our final model therefore accounted for 43.2% of the variability in the Leptospira river data, based on a pseudo-R2 using the Nagelkerke method [52, 53]. A summary of all four abiotic factors tested for each river (depth) or at each site (dissolved oxygen, temperature, and pH) are listed in S5 Table, which reports the median values of each one for those samples with Leptospira and for those without. Manabí Precipitation data were provided by the Instituto Nacional de Meteorologia e Hidrologia (INAMHI).
Soil experiment #1 - Leptospira prevalence and co-occurrence with other bacteria
Of the 64 dispersed soil samples collected in July and August of 2014, 14 were positive for infectious Leptospira and nine were positive for saprophytic Leptospira. In all cases, the detection was robust with an average Ct of 29.3 (range: 27–32) for infectious Leptospira and 27.4 (range: 24–32) for saprophytic Leptospira and seen in at least two of the four replicates for each sample.
Microbial community analysis of alpha diversity using Phylogenetic Diversity (PD) showed no difference in richness between samples that were positive versus negative for saprophytic Leptospira (Kruskal-Wallis H = 0.002, p = 0.959, q = 0.959); higher richness for soils that were positive for infectious Leptospira versus negative for infectious Leptospira (Kruskal-Wallis H = 8.19, p = 0.004, q = 0.014); and higher richness for samples that were positive for either infectious or saprophytic Leptospira versus negative for both (Kruskal-Wallis H = 6.19, p = 0.013, q = 0.026). Microbial community analysis of alpha diversity using Observed OTUs (OO) showed no difference in richness between samples that were positive versus negative for saprophytic Leptospira (Kruskal-Wallis H = 0.04, p = 0.838, q = 0.914); higher richness for soils that were positive for infectious Leptospira versus negative for infectious Leptospira (Kruskal-Wallis H = 11.58, p = 0.001, q = 0.012); and higher richness for samples that were positive for either infectious or saprophytic Leptospira versus negative for both (Kruskal-Wallis H = 7.50, p = 0.006, q = 0.014). PERMANOVA tests of unweighted UniFrac distances between samples illustrated minor differences in composition between samples that were positive versus negative for saprophytic Leptospira (pseudo-F = 1.34, p = 0.018, q = 0.031); minor differences in composition between samples that were positive versus negative for infectious Leptospira (pseudo-F = 1.44, p = 0.004, q = 0.014); and no difference in composition for samples that were positive for either infectious or saprophytic Leptospira versus negative for both (pseudo-F = 1.14, p = 0.127, q = 0.169). PERMANOVA tests of weighted UniFrac distances between samples illustrated minor differences in composition between samples that were positive versus negative for saprophytic Leptospira (pseudo-F = 2.54, p = 0.006, q = 0.014); no differences in composition between samples that were positive versus negative for infectious Leptospira (pseudo-F = 1.73, p = 0.064, q = 0.096); and no difference in composition for samples that were positive for either infectious or saprophytic Leptospira versus negative for both (pseudo-F = 0.90, p = 0.525, q = 0.630). While some of these results are suggestive of statistical significance, none are significant after Benjamini-Hochberg False Discovery Rate correction for the 12 results presented in this paragraph.
ANCOM analysis of the three sample groups (i.e., infectious, saprophytic, and infectious or saprophytic), identified taxa that were differentially abundant across the samples that were positive versus negative for each. An unidentified genus in the Acidobacterial order E29 (ANCOM W = 1034) and an unidentified genus in the NC10 (phylum) order MIZ17 (ANCOM W = 952) were present in higher abundance in infectious-Leptospira-positive samples than infectious-Leptospira-negative samples. The Cyanobacterial genus Arthronema (ANCOM W = 941) was present in higher abundance in the saprophytic-Leptospira-positive samples than saprophytic-Leptospira-negative samples. An unidentified genus in the Acidobacterial order E29 (W = 428) was also identified to be present in higher abundance in samples that were positive for either infectious or saprophytic Leptospira than in samples that were not negative for both. QIIME 2 artifacts and visualizations generated for microbiome analysis, and all QIIME 2 commands run for these analyses are available at https://github.com/caporaso-lab/ecuador-leptospira. The contained files can be viewed at https://view.qiime2.org.
Soil experiment #2 - Leptospira prevalence along water-shore transects
Infectious Leptospira were detected in 9 of 72 samples: 1 of 24 samples from the water and 8 of 48 from the shore (6 of 24 from the water-shore junction and 2 of 24 from higher on the shore). Saprophytic Leptospira was detected in only 2 of 72 samples, both from the shore (Fig. 2). We conducted a logistic regression to determine if any differences exist between the proportion of positive Leptospira samples discovered on the shore, at the water-shore junction, and in the river. For this analysis, we grouped infectious and saprophytic Leptospira types. We found that we were marginally more likely to find Leptospira at the water-shore junction compared to in the river (z = − 1.730, p = 0.083), and there was no difference between the proportion positive on the shore soil and at the water-shore junction (z = − 0.664, p = 0.507). Therefore, we are possibly more likely to find Leptospira in wet shore soil compared to in the river water itself.
Soil experiment #3 - Leptospira association with soil moisture content
High positivity of infectious Leptospira (40%) was detected in 25 shore soil samples collected within 1.5 m from the river. Positive samples had between 11.04 and 20.8% water content. Soils that tested positive for infectious Leptospira had a higher moisture content (M = 15.46, SD = 3.09) than samples that tested negative (M = 13.39, SD = 4.22), however, a logistic regression testing the effect of soil moisture on the presence of Leptospira did not show a significant effect (z-value = 1.186, p = 0.236; Fig. 1). This result is probably due to our small sample size and the narrow spread of observed moisture values.
Leptospira in river water
Rivers have long been associated with the transmission of leptospirosis, however, our data suggest that the contact with soil, rather than river water itself, may be more likely to result in transmission of Leptospira. In 112 samples from two rivers in the highly endemic province of Manabí, Ecuador, DNA from both infectious and saprophytic Leptospira were scarcely observed. This is despite the centrality of the two rivers to communities with high rates of leptospirosis. The paucity of Leptospira DNA in rivers is indicative of the lack of viable Leptospira, without which, rivers cannot contribute to the epidemiology of leptospirosis. These findings are consistent with the limited success of other efforts to find evidence of Leptospira in river water, with almost all positive samples being found near the shore, in small streams, stagnant water, or at very low concentrations [6, 8,9,10, 24, 25, 30, 33, 35, 54,55,56] . A limitation of our river sampling work is that the volume collected was not guided by the ability to detect a target concentration based on the infectious dose of Leptospira. The infectious dose of Leptospira is not known , nor is the degree to which likelihood of infection may be modulated by exposure time. However our detection of ~ 0.0125 Leptospira per mL (based on results from the four positive samples) is likely to be many orders of magnitude below the infectious dose, even under prolonged exposure.
Given this scarcity of infectious Leptospira species in the river, we searched for abiotic associations with all Leptospira as the shared evolutionary history of infectious and saprophytic Leptospira are likely to have resulted in many similar ecological qualities. In our study, the observed range of water temperature and dissolved oxygen were not associated with sample positivity. The observed pH values (7.4–8.8) are within a range at which Leptospira have been found previously [6, 9, 11, 29], but slightly above values systematically tested for survival times . Our results show a higher likelihood of finding Leptospira at the lower end of the observed range. Leptospira presence was also more likely in months where rainfall was high (see also ). This is consistent with an increase in leptospirosis cases following periods of high rainfall [27, 28, 57,58,59] which may be due to a general increase of viable Leptospira in the environment . The increased likelihood of our detection of Leptospira when river depths were lower may be due to a decreased dilution effect of Leptospira as well as increased dependence on the river and tributaries by livestock with fewer alternative sources of surface water.
Leptospira in shore soil
A much higher number of soil samples tested positive for infectious Leptospira (14 of 64 from Soil Experiment #1, 8 of 48 soil samples from Soil Experiment #2, and 10 of 25 soil samples from Soil Experiment #3) compared to river water samples (4 of 112 from our River Experiment and 1 of 24 of the river samples from Soil Experiment #2). Furthermore, the soil samples contained higher amounts of infectious Leptospira DNA. These results are consistent with a higher likelihood of finding infectious Leptospira in soils compared to canals and rivers . These results are highly suggestive of the relative importance of rivers and soils for transmission and environmental cycling.
It is possible that microbial communities influence the survival and persistence of infectious and saprophytic Leptospira. However after False Discovery Rate correction, we found no significant difference in species richness and overall community composition between samples that were positive or negative for Leptospira. We did however identify 2 uncharacterized genera from the orders E29 and MIZ27 that were found in higher abundance in samples containing infectious Leptospira. The E29 genus was also at higher abundance in samples with saprophytic Leptospira. A third genus (Arthronema), was present in higher abundance in samples containing saprophytic Leptospira. Unfortunately little is known about the ecological roles of these genera, making it difficult to speculate about ecological conditions that may provide insights into the presence or absence of Leptospira.
Our intensive soil sampling from two sites (Soil Experiment #3) showed a correlation between infectious Leptospira positivity and soil moisture, however this was not statistically significant, likely due to our small sample size and lack of samples with low moisture content. Comparing the presence of Leptospira along three transects of the Chico and Portoviejo rivers showed that pathogenic species were more likely to be found in samples taken from the water-shore junction than in the water, though this effect was marginal. This observation is consistent with our results suggesting the importance of high moisture content for the survival of infectious Leptospira. Our findings are also consistent with previous work on the importance of soil, soil moisture, and small puddles for the presence of infectious Leptospira [9, 22, 24, 25, 60]. This, coupled with the likelihood of finding infectious Leptospira in other shore samples, as opposed to the river itself, adds to evidence pointing to river shores as a larger threat of infection in these endemic communities of Manabí, Ecuador.
In this study, we aimed to explore the epidemiological importance of the riverine environment by testing for the presence of pathogenic Leptospira in the water column. Our results cast doubt upon the importance of river exposure in leptospirosis transmission. While many studies have demonstrated exposure to rivers as a risk factor [6,7,8,9,10,11,12,13,14,15,16,17,18,19,20,21], our findings lead us to conclude that the epidemiological role of rivers for Leptospira transmission may be limited compared to soils and river shores.
After being excreted via urine into the soil, direct contact with Leptospira contaminated soil may result in transmission. The likelihood of transmission will depend on the environmental persistence of sufficiently high concentrations of Leptospira needed to cause infection. If shed directly into a river or subsequently washed into one, Leptospira will be severely diluted, decreasing the likelihood of infection. Environmental persistence is critical, and rains may prime the soil to maximize Leptospira survival, thereby expanding the time window where contact can lead to transmission. This mechanism may explain our increased detection, as well as the higher number of clinical cases, associated with precipitation.
Our work here specifically addresses the role of the water column in rivers, but our conclusions may be generalizable to other parts of the river (near the shore or benthic area) as well as large bodies of water whereby entering Lepospira will be severely diluted. For example, strong epidemiological links to a reservoir led to subsequent investigations that only revealed molecular or microbiological evidence of Leptospira in the shore soils, rather than in the water itself . Similar to our conclusions regarding rivers, we suspect that the epidemiological role of lakes and reservoirs is limited. We therefore hypothesize that water-associated behavior, which often entails walking barefoot on the shore, provides an avenue for contact with moist soil that may harbor high concentrations of Leptospira and result in transmission. Similarly, flooding is commonly associated with leptospirosis outbreaks as flood waters can contain and disperse high concentrations of Leptospira from overflowing sewers and flooded agricultural areas [61,62,63]. Importantly, the widespread tendency to remove shoes during floods may put high numbers of people at particular risk for infection.
There are a few notable limitations of this work and its implications. Firstly, river samples were collected from the water column and not the sediments. As such, we cannot assess the likelihood of Leptospira in benthic material. Secondly, there is still much to discover about the diversity of Leptospira and how Leptospira presence in the environment translates into human infections [64,65,66]. It is possible that a scarcity of the pathogen in rivers does not necessarily lead to a lower likelihood of transmission if, for instance, the presence of water makes skin more easily penetrable, or if highly concentrated biofilms occur. Thirdly, the infectious dose for any Leptospira species across any host is not known . Fourth, this study incidentally captures the environmental circumstances at a time with abnormally low rainfall and less than average number of leptospirosis cases, possibly limiting how representative our results are of a typical year. Lastly, little is known about Leptospira survival in soils and the conditions in which it survives best. Despite these limitations, our work suggests that soil, rather than river exposure, may be more epidemiologically important. While these conclusions might be generalized across to other bodies of water, it is important to recognize the possibility, and associated epidemiological risk, for the accumulation of Leptospira in stagnant water sources [10, 11]. Additional work directed at testing the long-held assumption of the relevance of water exposure, and the importance of contact with moist soil should be prioritized as we work to more fully understand and control transmission.
Availability of data and materials
The datasets used and/or analysed during the current study available at: 1) Sequences alignment of Leptospira spp. fragment amplified for Sapro assay http://purl.org/phylo/treebase/phylows/study/TB2:S27108?x-access-code=263709726a7b3481e9de706185eb102f&format=html. 2) Microbial community analysis https://www.dropbox.com/s/gb97xbv1ieija7z/barragan-et-al-sequence-data.zip?dl=0
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This work was funded by National Institute of Allergy and Infectious Disease, National Institutes of Health, grant R15AI101913; a SENESCYT scholarship from the Ecuadorian Government; and the Universidad San Francisco de Quito Ecuador. Salary support for T. Pearson was provided, in part by NIH/NIMHDRCMIU54MD012388. The funders had no role in study design, data collection and analysis, decision to publish, or preparation of the manuscript.
We thank Manuelito Velez for his help with field work and Francisca Cedeño for allowing us to place the water sensor on her property. We also thank Andrea Encalada from the Instituto Biosfera in the Colegio de Ciencias Biologicas y Ambientales, of the Universidad San Francisco de Quito for her advice and guidance in establishing river data collection protocols.
The authors declare no conflict of interest.
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Miller, E., Barragan, V., Chiriboga, J. et al. Leptospira in river and soil in a highly endemic area of Ecuador. BMC Microbiol 21, 17 (2021). https://doi.org/10.1186/s12866-020-02069-y