Skip to main content
  • Research Article
  • Open access
  • Published:

Cryptosporidiosis threat under climate change in China: prediction and validation of habitat suitability and outbreak risk for human-derived Cryptosporidium based on ecological niche models



Cryptosporidiosis is a zoonotic intestinal infectious disease caused by Cryptosporidium spp., and its transmission is highly influenced by climate factors. In the present study, the potential spatial distribution of Cryptosporidium in China was predicted based on ecological niche models for cryptosporidiosis epidemic risk warning and prevention and control.


The applicability of existing Cryptosporidium presence points in ENM analysis was investigated based on data from monitoring sites in 2011–2019. Cryptosporidium occurrence data for China and neighboring countries were extracted and used to construct the ENMs, namely Maxent, Bioclim, Domain, and Garp. Models were evaluated based on Receiver Operating Characteristic curve, Kappa, and True Skill Statistic coefficients. The best model was constructed using Cryptosporidium data and climate variables during 1986‒2010, and used to analyze the effects of climate factors on Cryptosporidium distribution. The climate variables for the period 2011‒2100 were projected to the simulation results to predict the ecological adaptability and potential distribution of Cryptosporidium in future in China.


The Maxent model (AUC = 0.95, maximum Kappa = 0.91, maximum TSS = 1.00) fit better than the other three models and was thus considered the best ENM for predicting Cryptosporidium habitat suitability. The major suitable habitats for human-derived Cryptosporidium in China were located in some high-population density areas, especially in the middle and lower reaches of the Yangtze River, the lower reaches of the Yellow River, and the Huai and the Pearl River Basins (cloglog value of habitat suitability > 0.9). Under future climate change, non-suitable habitats for Cryptosporidium will shrink, while highly suitable habitats will expand significantly (χ2 = 76.641, P < 0.01; χ2 = 86.836, P < 0.01), and the main changes will likely be concentrated in the northeastern, southwestern, and northwestern regions.


The Maxent model is applicable in prediction of Cryptosporidium habitat suitability and can achieve excellent simulation results. These results suggest a current high risk of transmission and significant pressure for cryptosporidiosis prevention and control in China. Against a future climate change background, Cryptosporidium may gain more suitable habitats within China. Constructing a national surveillance network could facilitate further elucidation of the epidemiological trends and transmission patterns of cryptosporidiosis, and mitigate the associated epidemic and outbreak risks.

Graphical Abstract


Cryptosporidiosis is a global zoonotic parasitic disease caused by protozoan infections of Cryptosporidium spp. of the phylum Apicomplexa. Cryptosporidium can infect humans directly or indirectly through the fecal–oral route [1]. After entering the host, oocysts normally parasitize intestinal epithelial cells, and can cause acute gastroenteritis, abdominal pain, and diarrhea in humans [2]. Because of its highly infectious and transmissible nature, in addition to high resistance to disinfectants, cryptosporidiosis is an acute infectious disease of major concern to the international community [3]. Because cryptosporidiosis prevalence is influenced by public health conditions, it is often significantly more prevalent in low-income countries and regions, and constitutes an emerging poverty-induced parasitic disease [4]. In China, the first indigenous case of cryptosporidiosis was reported by Han et al. in 1987 [5]. As of 2018, Cryptosporidium infection has been reported in most provincial administrative regions in China [6]. Therefore, the disease has continuously attracted the attention of government departments and public health institutions [7]. However, due to the lack of a routine surveillance system for cryptosporidiosis, the epidemic status of cryptosporidiosis in China remains unclear [8]. Therefore, spatial model predictions based on existing data can provide theoretical support for further prevention and control programs.

Due to the lack of systematic national epidemiological surveys on cryptosporidiosis, the existence of Cryptosporidium in certain regions can only be determined based on existing data; however, there is no way of demonstrating that Cryptosporidium has never occurred in a region. For such “presence-only” data, ecological niche models (ENMs) may be the most suitable types of spatial simulation methods [9]. ENMs rely on available biogeographic information to project the environmental conditions (i.e., ecological niches) that allow organisms to survive and reproduce, and ultimately project such conditions onto the actual landscape to simulate suitable habitats [10]. Common correlational models include the Bioclimate (Bioclim) model, in which the ecological niche is defined as a hyper-rectangular range defined by the extreme values of each environmental variable [11]; a model based on genetic algorithms for rule-set production (Garp), which primarily utilizes species distribution and environmental data to run sets that produce different rules to determine the ecological needs of species and predict their potential distribution in space [12]; the Domain model, which is based on the Gower algorithm, uses a point-to-point similarity matrix to calculate the suitability of environmental variables at the target point, and obtains a discontinuous distribution interval by setting the threshold value [13]; and the maximum entropy (Maxent) model, which is based on the second law of thermodynamics, introduces the concept of information entropy, and fits the probability distribution with the maximum entropy value as the predicted species distribution [14]. Today, the application of ENMs is no longer limited to ecological studies of plants and animals, and epidemiological studies increasingly attempt to adopt and enrich ENM methods [15].

Compared to spatial epidemiology, ENMs in addition to being able to predict disease transmission risk, can determine landscape factors of disease prevalence and predict pathogen distribution patterns under environmental change scenarios [16]. This is particularly true for parasites and parasitic diseases. For example, various protozoa and helminths, such as Toxoplasma gondii, Giardia lamblia, Trypanosoma cruzi, Fasciola spp., Anisakis spp., and their respective hosts, have been analyzed using ENMs with satisfactory results [17,18,19,20]. Meanwhile, researchers have applied ENMs to predict the risk of common parasitic diseases such as malaria, trypanosomiasis, schistosomiasis, onchocerciasis, and filariasis [21, 22]. Therefore, ENMs have played a significant role in parasite control planning [23]. Notably, there is reportedly a significant correlation between Cryptosporidium bio-adaptation and climate, mainly reflected in the influence of temperature and precipitation (humidity) on activity, survival time, and dispersal dynamics of oocysts after excretion by the host and directly exposed to the environment [24,25,26]. For example, in areas with mild climate, the density of Cryptosporidium oocysts and the incidence of cryptosporidiosis may be positively correlated with temperature; specifically, the temperature may be the highest monthly temperature, the average temperature in the wet season, or even the average temperature in the previous 1–3 months. In other regions (such as North America), the study found that the survival rate and infectivity of oocysts in the environment were negatively correlated with temperature, because higher temperatures increased the mortality of Cryptosporidium oocysts [27, 28]. In Australia, there is a correlation between temperature and cryptosporidiosis incidence in rural areas, but not in urban areas. Furthermore, precipitation may also be correlated to Cryptosporidium; in equatorial and subtropical regions, the concentration of Cryptosporidium oocysts and the incidence rate of cryptosporidiosis are positively correlated with rainfall. Extreme weather can increase the concentration of oocysts, and heavy rainfall may cause the outbreak of cryptosporidiosis. In temperate regions, precipitation may dilute the concentration of cryptosporidium oocysts through surface water flows, resulting in a negative correlation between incidence rate and rainfall [27, 28]. Jagai et al. reported that in humid tropical climates, precipitation is a key driver of seasonal cryptosporidiosis, and the incidence of cryptosporidiosis in temperate climates peaks at high temperatures [29]. This biological characteristic of Cryptosporidium provides for a chance to use ENMs to predict its spatial distribution under a climate change background.

Actually, many zoonotic diseases caused by parasites are vulnerable to changes in climate, partially because of direct exposure to climate conditions in their free-living stages [30]. Climate change may be key factors affecting parasite survival, leading to parasite co-extinction, redistribution, or emergence of new infectious diseases [31]. Within some regions, parasite abundance may even increase by an order of magnitude, and some studies have successfully traced parasite invasion from tropical regions to temperate ecosystems during climate change, with native species replaced during climate change, with unpredictable ecological consequences [32]. Therefore, it is considered one of the most pressing theoretical problems in parasitic epidemiology to understand the dynamics of prevalence patterns and the distribution of parasites under climate change [33]. In the present study, we focus on Cryptosporidium survival trends in the context of climate change, specifically including how applicable are ENMs; how do climatic factors play a role; and what are the spatial distributions in past, present, and future periods in ecological adaptation analysis of Cryptosporidium? This is a notable attempt to apply ENMs in simulating the potential spatial and temporal distributions of Cryptosporidium, an important parasite with a relatively weak research foundation in China.


Extraction of bioclimatic variables

Nineteen common bioclimatic variables have been summarized based on the Assessment Report of the Intergovernmental Panel on Climate Change (IPCC), which are mainly deduced from temperature and precipitation data and can reflect the environmental constraints and their impacts on organism distribution and survival [34]. Such climate data can be obtained from the WorldClim database ( [35] and downloaded from the Climatologies at the High Resolution for the Earth’s Land Surface Areas (CHELSA) database ( [43]. In the present study, the latest versions 2.1 of the two databases were used to develop the model. For the future climate data projections in both databases, a more conservative scenario, SSP126, and a more effective simulation model, MRI-ESM2-0, were selected for use in the ENMs [37, 38]. See Additional file 1 for details.

Grid selection of climate variables

Three sentinel hospitals were selected for patient data collection. The hospitals were located in Shanghai (provincial district in China), Zhenjiang (municipal), and Danyang (county), and were denoted as Hosp1, Hosp2, and Hosp3, respectively [39]. The data included results of Cryptosporidium detection and long-term address information of patients with diarrhea. First, the permanent addresses were imported into Google satellite maps ( for conversion into latitude and longitude coordinates, and then loaded into ArcMap of the ArcGIS v10.8 (ESRI Inc., Redlands, CA, USA) [40]. A point distance analysis tool was used to obtain the straight-line distance from the residence of patients to the hospitals. The Shapiro–Wilk (SW) and Levene’s tests were performed in IBM SPSS Statistics v26 (IBM Corp., Armonk, NY, USA) to observe the data distribution characteristics and homogeneity of variance [41]. Finally, box violin distribution plots were generated using Hiplot v0.2.0 (TengyunBioTech Ltd., Shanghai, China) to visualize the results [42]. The procedure was aimed at assessing the feasibility of the location coordinates of health care facilities as occurrence points of Cryptosporidium and selection of the spatial scales of the variables.

Occurrence point data collection

Two types of publicly available historical data were collected: (i) Cryptosporidium-related studies and reports in China were obtained from PubMed database (, ResearchGate database (, the China National Knowledge Infrastructure (CNKI) ( database, the Wanfang Database (, and the China Science and Technology Journal Database ( by searching the following keywords: Cryptosporidium, cryptosporidiosis, diarrhea pathogen, intestinal protozoa, intestinal parasite, China, and province names in China; duplicate reports were removed. The remaining articles were carefully reviewed to screen relevant articles on human-derived Cryptosporidium or cryptosporidiosis in China. Articles (such as reviews and some basic research) from which reliable investigation periods and locations could not be extracted were excluded. To enhance the prediction level of models, Cryptosporidium survey data were collected from countries neighboring China from the PubMed database. Similar search and inclusion criteria were used in this section, excluding China being replaced with the other countries. Subsequently, if the sampling site was a hospital or another health care institution, and Cryptosporidium infection in patients attending the hospital was confirmed, the location coordinate of the institution was included as a Cryptosporidium occurrence point. If a Cryptosporidium infection was detected through field investigation, the coordinate of the investigation site was collected as an occurrence point. Latitude and longitude information and raster information of environmental factors were analyzed using ENMTools v1.4.4 to eliminate redundant points and to reduce their impact on model accuracy and reliability [43]. The cleaned data were imported into ArcMap to map the point distribution and case report areas of Cryptosporidium in China.

Bioclimatic variable screening

Correlation between occurrence points and environmental variables potentially exists in the data. If the collinear variables are not screened, it can lead to model over-fitting [44]. In the present study, due to the variable interpretation requirement, the contribution value of each variable and the correlation coefficient between variables are considered comprehensively to exclude the collinear variables, instead of the principal component analysis method [45]. The percentage contribution (PC) of environmental factors to the model prediction results was assessed using the Jackknife method [9]. Subsequently, variable information for each point was extracted using ArcMap and imported into IBM SPSS Statistics 26 [41] to calculate the Pearson Correlation Coefficients (PCCs) among the variables. The contribution point plots and correlation heat maps of environmental variables were plotted using Hiplot v0.2.0 [42]. Among the variables with absolute correlation coefficients |r|≥ 0.8, only the variable with the largest contribution was retained [9].

ENMs evaluation and selection

In the present study, an aggregate of four ENMs was tested. Maxent v3.4.3 (American Museum of Natural History, New York, USA) was used for the Maxent model [46], DIVA-GIS v7.5.0 was used for the BIOCLIM and Domain models [47], and DesktopGarp v1.1.6 was used for the Garp model [48]. The previously screened effective Cryptosporidium occurrence points were divided into two datasets: one had coordinate points collected from literature and imported for model construction, and another extracted from sentinel hospitals for use in evaluating model effectiveness. All the data, variables, and set parameters were maintained at default when calculating the four models, and predictions by each model were repeated 10 times. Finally, the test data and simulation results were imported into Niche Analysis v3.0 to plot the Receiver Operating Characteristic (ROC), Kappa, and True Skill Statistic (TSS) curves [49], and to further calculate the area value under ROC curve (AUC, the closer this value is to 1.00, the more accurate the results predicted by the model), maximum Kappa value (the closer this value is to 1.00, the better the consistency of the model), and TSS value (the closer this value is to 1.00, the more excellent the discrimination ability of the model) [50,51,52]. Scatter plots were drawn using Hiplot v0.2.0 [42].

Parameter optimization of model

The two parameters that significantly impact model prediction results are Feature Combination (FC), including linear (L), quadratic (Q), hinge (H), product (P), and threshold (T), and Regularization Multipliers (RM) from 0.5 to 4.0 [53,54,55]. In the present study, the RM values were set from 0.5 to 4.0, with a 0.5 increase for each simulation. FC was simulated using seven combinations: H, L, LPQ, LQ, LQH, LQHP, and LQHPT. The final simulation results were evaluated using ROC and information criterion (IC). The ROC evaluation indexes include the AUC during model testing (AUCTest, larger values indicate better effects), which evaluates model performance under different threshold conditions, and the AUC difference between the training and test datasets (AUCDiffer, lower values indicating greater gains), which evaluates the risk of overparameterization. The IC evaluation indexes were used to measure model complexity and goodness of fit, which include the sample size-corrected Akaike IC (AICc) and the Bayesian IC (BIC), and lower values suggest better balance between goodness of fit and reduced free parameters [53]. Matrix plots were visualized using Hiplot v0.2.0 [42].

Effects of environmental variables on Cryptosporidium distribution

Cryptosporidium occurrence points were extracted from surveys conducted between 1986 and 2010, and were imported into the Maxent software. Historical climate data from CHELSA v2.1 (for the 1981‒2020 period) were selected. Climate variables and parameters were set according to the results of previous steps. Twenty-five percent of the random points were selected as the test data. The maximum number of background points was set as 10,000, the model was bootstrapped 100 times, and the results were obtained in cloglog format, a more effective format in explaining the prediction omission rate, to enable the calculation of the response curves of the variables used for modeling [56].

Habitats currently suitable for Cryptosporidium in China

Based on the simulation results of data from 1986 to 2010, climate data layers from 2011 to 2040 were projected onto the model with the largest AUC value to predict the potential distribution of Cryptosporidium under current climate conditions. The occurrence points from 2010 to 2021 were imported into the prediction results as the test set to evaluate the effectiveness of the model. The final prediction results were imported into ArcGIS v10.8 [45], which was used to extract predicted Cryptosporidium maps within China. The average pixel values (Cloglog values) in the local spatial range were extracted from the county-level, city-level, and provincial-level areas to analyze current Cryptosporidium distribution in China.

Potential distribution of Cryptosporidium in future

Based on the simulation results using climate data from 1981 to 2010, the future bioclimate variables provided by two climate data databases (WorldClim and CHELSA) were analyzed separately. The geographical areas of suitable habitats were calculated using ArcGIS v10.8 [40]. The areas were mapped using Hiplot v0.2.0 [42]. Chi-square (χ2) tests were performed to test differences in distribution areas during different periods using IBM SPSS v26 [41], and P-values were corrected using the Bonferroni method. The standard deviation of the predicted cloglog values of suitable area over four periods (1981‒2010, 2011‒2040, 2041‒2070, and 2071‒2100) were calculated using ArcGIS v10.8 [40] to analyze the degrees of variation in different areas. In addition, differences in predictions between two adjacent time periods were calculated and used to analyze changes in suitable Cryptosporidium habitats.


Spatial scale of climate variable on the map

The straight-line distance data between the place of residence and the hospital selected by diarrhea patients did not follow a normal distribution (W = 0.121, P < 0.01) and exhibited heterogeneous variance (L = 5.213, P < 0.01), potentially because the patients included travelers from other places or temporary visitors. Hence, the median of logarithmic distance was selected to describe the data as a whole. As shown in Fig. 1a, using hospitals as the center points, the median distances for patients seeking medical advice were 5754.40 m (95% CI: 5596.75‒6007.88), 6456.54 m (95% CI: 6098.82‒6806.41) and 8317.64 m (95% CI: 7974.43‒8841.42) for Hosp1, Hosp2 and Hosp3, respectively. In contrast, distance data from 37 Cryptosporidium-infected patients were normally distributed (W = 0.966, P = 0.320) and exhibited homogeneous variance (L = 5.213, P < 0.01). Therefore, the average distances were 6092.95 m (95% CI: 4625.06‒7560.84) and 11,091.17 m (95% CI: 9190.44–12,991.90) for Hosp 1 and Hosp 3, respectively (Fig. 1b). The results indicate that the variable raster base map of 5 min (approximately 9 km × 9 km) can accommodate environmental information, with the hospital as the center point, and ensure prediction accuracy.

Fig. 1
figure 1

Box-violin diagram based on straight-line distance between patient residences and hospital visited. a Logarithmic distance between diarrhea patient residences and three hospitals. b Distances of travel of Cryptosporidium-infected patients during visits to Hosp1 and Hosp3 (no Cryptosporidium infection was detected in patients with diarrhea at Hosp2)

Data collection and variable screening

In the present study, a total of 474 coordinate points related to the distribution of Cryptosporidium were extracted from the 243 collected research articles (see Additional file 2) and detection data of sentinel hospitals. After eliminating redundant data, 377 valid points were incorporated into the 5-min variable raster, including 228 points within China and 149 points within neighboring countries (see Additional file 3). To match the time nodes of periodic climate data obtained from the WorldClim and CHELSA databases, all points were classified into 154 points reported during 1986‒2000, 266 points reported during 1986‒2010, and 111 points reported during 2011‒2021, based on the survey date. Cryptosporidium-infected individuals were reported in 105 municipal administrative regions in 29 provincial administrative regions in China. In addition, to safeguard the privacy of participants, the specific addresses and coordinates of infected individuals were not included. Instead, only the area information are described in Additional file 4 and Additional file 5. After considering the average percentage contribution, and excluding possible collinearity of 19 bioclimatic variables observed, 10 variables were input in the simulation model, namely bio13 (precipitation of wettest month), bio1 (annual mean temperature), bio18 (precipitation of warmest quarter), bio5 (maximum temperature of warmest month), bio15 (precipitation seasonality), bio19 (precipitation of coldest quarter), bio8 (mean temperature of wettest quarter), bio2 (mean diurnal range), bio3 (isothermality), and bio14 (precipitation of driest month), which included five temperature-related variables and five precipitation-related variables (see Additional file 6).

Model effectiveness

Among the four modeling approaches tested in the present study, the Maxent, BIOCLIM, and Domain models achieved the maximum TSS value of 1.00 for each run, whereas the mean of the maximum TSS values for the Garp model was 0.95 (95% CI: 0.92‒0.97). As shown in Fig. 2, the Maxent model outperformed the other three models in prediction accuracy (0.95 AUC value with a range of 95% CI: 0.94‒0.97) and consistency (0.91 maximum Kappa value with 95% CI from 0.88 to 0.95).

Fig. 2
figure 2

Scatter plots of AUC and maximum kappa values for four ecological niche models. AUC is the area under curve of receiver operating characteristic; Maxent is maximum entropy model; Bioclim is bioclimate model; Domain is domain model; Garp: the model based on genetic algorithms for rule-set production

Model optimization and construction

Two combinations of each index value ranked in the top 10 out of 56 parameter combinations of FC and RM were preferred, namely LPQ-0.5 and LPQ-1.0. Subsequently, the combination with superior AUCTest and AICc values, namely LPQ-1.0, was selected (Fig. 3) to construct the Maxent model, and the simulation results with an average AUC of up to 0.939 ± 0.005 were finally obtained (Additional file 7). Therefore, compared with the optimized parameter settings (LPQ-1.0), the default model parameter setting (LQHP-1.0) did not yield optimal simulation results in the present study.

Fig. 3
figure 3

AUCTest, AUCDiffer, AICc, and BIC matrix heat maps of models with different Regularization Multipliers (RM) parameters on Y-axes and Feature Combination (FC) parameters on X-axes in Maxent model. AUCTest refers to the AUC (area under the receiver operating characteristic curve) obtained by the ENM in the testing procedure; AUCDiffer refers to the AUC difference between the training operation and the test operation; AICc: corrected Akaike information criterion; BIC: Bayesian information criterion

Environmental effects on Cryptosporidium distribution

The contributions of bio1, bio2, bio8, and bio18 to the model all exceeded 10%, and the cumulative contribution of the four factors was > 80%. Based on the prediction results, a cloglog value of 0.1 was set as the threshold for suitable Cryptosporidium habitats. When all other environmental variables were maintained at their mean values, the independent environmental factor response curves showed that the lowest annual mean temperature (bio1) at which Cryptosporidium could stably survive was 3.68 °C. Furthermore, the probability of survival increased with an increase in temperature. The maximum survival gain was obtained at 15.65 °C, with further temperature increases decreasing survival. When the temperature was higher than 27.64 °C, the habitat was no longer suitable for Cryptosporidium survival (Fig. 4a). When the bio1 was input into the model for comprehensive consideration, the survival temperature range was broader (− 0.76–33.37 °C) and the optimal response peak increased to 16.41 °C (Fig. 4k). The mean diurnal range represented by bio2 was suitable for Cryptosporidium, at 2.17–14.28 °C, with an optimum temperature of 8.20 °C (Fig. 4b). However, other variables in the model may compensate for the limitations of this variable for species distribution to some extent, thereby expanding the suitable temperatures to 0.87–15.99 °C and increasing the optimum temperature to 9.15 °C (Fig. 4l). The minimum temperature at which Cryptosporidium could stably survive during the season with the highest humidity (bio8) was 6.01 °C and the optimum survival environment was 26.03 °C (Fig. 4e); however, the variable does not limit Cryptosporidium survival in the comprehensive assessment of the model (Fig. 4o). Considering the specific heat capacity of water and the water-borne transmission of Cryptosporidium, the effects of temperature variation on the probability of Cryptosporidium survival may be offset by humidity; therefore, this result is reasonable. A similar variable is bio18, in which the maximum precipitation at which Cryptosporidium can stably survive during the warmest season is 4775.78 mm (Fig. 4i). After considering the interaction of each variable, Cryptosporidium could survive in the extreme conditions of bio18 (Fig. 4s), probably because warmer temperatures enhance Cryptosporidium reproduction and dispersal, thus offsetting forced oocyst migration caused by high precipitation. Although the extreme conditions are breached, the survival probability of Cryptosporidium is still affected by bio8 and bio18.

Fig. 4
figure 4

Response curves of 10 environmental variables included. A–J Independent response curves for environmental factors when all other environmental variables remain at their mean sample values. K-T Response curves for environmental variables used in model construction

Current potentially suitable habitats for Cryptosporidium

The simulation prediction had an AUC of 0.947 and a maximum kappa value of 0.789 from 2011 to 2040, indicating that the model had good prediction effects, strong transferability, and high consistency, and can be used to describe and analyze current Cryptosporidium distribution. A cloglog value of 0.1 was set as the threshold for suitable Cryptosporidium habitats based on the results of the Maxent run. Considering Cryptosporidium may leave its native habitat via water flows and human activity, a more stringent threshold for areas with high habitat suitability (cloglog = 0.9) was selected. In addition, 0.1‒0.5 was set as the range for areas with low habitat suitability and 0.5‒0.9 was used for areas with moderate habitat suitability. The final results indicated that the areas with high habitat suitability for Cryptosporidium in China at this stage were primarily concentrated in Eastern and Central China including the entire regions of Jiangsu, Anhui, Shandong, Jiangxi, Henan and Hubei provinces, and Tianjin City, in addition to some cities in Hebei, Liaoning, Zhejiang, Hunan, Guangdong, Sichuan and Guangxi provinces. They were also concentrated in some districts and counties in the municipalities of Beijing, Shanghai, and Chongqing, and were sporadic in some regions in Jilin, Fujian, and Guizhou provinces. Non-suitable habitats included most of the Qinghai–Tibet Plateau, Hexi Corridor (most of Gansu Province), northern Heilongjiang Province, western Inner Mongolia Autonomous Region, and northern and southwestern Xinjiang Autonomous Region. Areas with moderate habitat suitability included areas outside the highly suitable and non-suitable habitats of all provincial administrative regions associated with high habitat suitability, also including southwestern Heilongjiang Province, southern Shanxi Province, central and southern Shaanxi Province, eastern Yunnan Province, southeastern Gansu Province, eastern Inner Mongolia Autonomous Region, Hainan and Taiwan islands, and Hong Kong Special Administrative Region. Areas with low habitat suitability were regions other than the aforementioned areas. In addition, all cities with high, moderate, and low habitat suitability for human-derived Cryptosporidium in China are listed in the supplementary file to support actual cryptosporidiosis control and prevention (see Additional file 8). In terms of geographical pattern, Cryptosporidium distribution areas were primarily located along the middle and lower reaches of the Yangtze River, the lower reaches of the Yellow River, and the Huai and the Pearl River Basin. Considering population development level and economic and social patterns, Cryptosporidium was mainly distributed below the Hu–Line (Heihe–Tengchong Line) [57], which is a region with high population density (see Fig. 5).

Fig. 5
figure 5

Predicted suitable habitats for Cryptosporidium in China at the present stage (2011‒2040). a Receiver Operating Characteristic (ROC) curves. b Kappa curves. c Heat maps of habitat suitability for Cryptosporidium. d Distribution of suitable habitats for Cryptosporidium by county-level administrative regions

Prediction of future Cryptosporidium distribution

Under a climate change background, variation in the areas of habitats with moderate suitability was minor; shifts in the area of habitats were mainly reflected in decreasing areas of non-suitable habitats and expansion of areas of highly suitable habitats (Fig. 6a). The results indicate that Cryptosporidium will gain more suitable habitats in China in future (see Additional file 9 for details). As shown in Fig. 6b, variations in suitable habitats for Cryptosporidium from 1981 to 2100 were mainly concentrated in the northeastern, southwestern, southern, northwestern, and northern regions of China, with less changes in the eastern and Qinghai-Tibet Plateau areas. Furthermore, as illustrated in Fig. 6c-1, Cryptosporidium exhibited increased adaptation to climate in northeastern China, the coastal areas of northern China, and the edge of the Sichuan Basin from 2011 to 2040, relative to that from 1981 to 2010; conversely, reduced adaptation was observed in southwestern China, the coastal areas of southern China, and northwestern China, using an absolute value of the cloglog difference of 0.1 as the threshold for habitat suitability. Relative to that from 2011 to 2040, the predicted climate status from 2041 to 2070 is more favorable for Cryptosporidium survival in northern, northwestern and southwestern China, and along the coast of southern China (Fig. 6c-2); and areas with reduced survival probability were few. Figure 6c-3 shows the change in 2071‒2100 relative to the status in 2041‒2070: habitat suitability increased in Heilongjiang, Hainan, and coastal areas of Southern China, whereas Cryptosporidium survival probability decreased in northern Yunnan and central Xinjiang.

Fig. 6
figure 6

Predicted suitable habitats for Cryptosporidium based on future climate data. a-1 Area maps of suitable habitats at each level based on climate data from the Climatologies at High Resolution for the Earth’s Land Surface Areas (CHELSA) database for four periods (1981‒2100). a-2 Area maps of suitable habitats at each level based on climate data from the WorldClim database for four periods (2021‒2100). b The standard deviation of habitat suitability (Cloglog) based on CHELSA database simulations for four periods (1981‒2100). c-1 Changes in habitat suitability based on the CHELSA database for the 2011‒2040 period relative to the 1981‒2010 period. c-2 Changes in habitat suitability based on the CHELSA database for the 2041‒2070 period relative to the 2011‒2040 period. c-3 Changes in habitat suitability (Cloglog) based on the CHELSA database for the 2071‒2100 period relative to the 2041‒2070 period. The absolute value of the cloglog difference of 0.1 was used as the threshold for habitat suitability in picture c-1/c-2/c-3


In the present study, a systematic ENM simulation for suitable Cryptosporidium habitats was conducted. Several key variables were tested and analyzed, in addition to data collection, screening, and collation; data applicability analysis; selection and calibration of environmental factor databases; and model selection, optimization, simulation, and evaluation. All defects and loopholes in the model simulation process were considered and avoided as much as possible. The final results indicated that the Maxent model with adjusted parameters returned the best simulation results with high evaluation indexes. The result confirms that ENMs can be applied to predict potential Cryptosporidium distribution, thereby providing insights and new methods for further research, and Cryptosporidium infection prevention and control. Moreover, when simulating parasitic infectious diseases using ENMs, it is necessary to assess which environmental variables may be meaningful using established information, while accounting for the biological characteristics of parasites, adopting reasonable spatial scales, performing spatial and temporal matching with species presence data, and ensuring data accessibility [23]. This is why we devote a lot of space in the Methods section to explaining the model running procedure.

According to the present study, at a macroscopic geographic scale, there are three areas with high suitability for human-derived Cryptosporidium in China: the plains in eastern China, the Pearl River Basin, and the Sichuan Basin. Notably, the areas are also high population areas. In addition, there is a clear unsuitable habitat zone, namely the Qinghai–Tibet Plateau, where the unique alpine climate limits Cryptosporidium survival and dispersal. The northeastern (Jilin and Heilongjiang Provinces), southwestern (Yunnan Province), and northwestern (Xinjiang Autonomous Region) regions are considerably affected by climate change, which may result in shifts in Cryptosporidium habitat suitability. It is critical to clarify that all projections of future climate change are based on simulations of historical data from 1981 to 2010, and only projections for the period from 2011 to 2040 can be verified using existing data. Therefore, the projections for the current period (2011–2040) are relatively reliable when compared to those of other periods (2041–2100) without test data. However, the fact that suitable Cryptosporidium habitats are expanding in China should not be overlooked. The species has gained survival benefits from climate change and may become widespread in future. Original parasite transmission dynamics may be disrupted and reshaped during climate change events. In addition, ongoing genetic evolution will lead to the emergence of subspecies and genetic subtypes that are adaptable to new environments and have increased potential for host switching [58]. Furthermore, new ecological fitting patterns may lead to more frequent transmission between humans and animals, which, in turn, would lead to unknown Cryptosporidium transmission risk in future, and make forward-looking research challenging. Therefore, continuous climate monitoring, dynamic “Cryptosporidium–environment” fitting studies, and time- and place-specific prevention, control, and planning activities could facilitate coping with the potential threat. In addition, seasonal variation in Cryptosporidium prevalence in different regions within China is irregular [6], which is also observed in India [59]. Identifying suitable habitats for Cryptosporidium may help explain this phenomenon; for example, the time required to reach suitable environmental conditions for Cryptosporidium spread is not consistent between high and low latitude or altitude areas, leading to uncertainty in the seasonal factors driving Cryptosporidium infection. Such inter-regional diversity is normal in a country as vast as China.

Areas with high habitat suitability provide conditions suitable for the survival of Cryptosporidium; therefore, the public health risk caused by cryptosporidiosis is relatively high in such areas. It may result in Cryptosporidium outbreaks even if a small number of infectious agents (infected individuals) are not controlled in time. Therefore, in such areas, a high degree of sustained monitoring is necessary. Cryptosporidiosis is also prevalent within areas with moderate habitat suitability. However, the periods suitable for Cryptosporidium survival may not be perennial in such areas; instead, the transmission risk of cryptosporidiosis may be significantly higher during warm and humid periods than in the other periods. In contrast, in areas with low habitat suitability, the survival space for Cryptosporidium is compressed; cryptosporidiosis transmission and infection may occur in months when conditions are suitable, with a low probability of outbreaks. Notably, Cryptosporidium infections may also occur in areas with unsuitable habitats, for example, when pathogens are carried into an area by travelers, with small-scale transmission potentially occurring by direct contact or indirect contact over a short period. When discussing the actual risks of cryptosporidiosis outbreak, practical factors, such as local population density, public health services and numbers of animal hosts should also be taken into account [60]. Therefore, the results of the present study based on models do not indicate the probability of finding Cryptosporidium species (oocyst) in a given location but provide a habitat suitability index (i.e., habitat quality for species survival and persistence) [9]. The results reflect whether the environmental conditions in a region are favorable for Cryptosporidium survival and spread when the pathogen is present, from which the likelihood of prevalence and outbreaks can be inferred.

Cryptosporidiosis is endemic globally and is among the most extensively distributed intestinal parasites, with an overall global prevalence of approximately 7.6% (95% CI: 6.9‒8.5) [4]. From 2009 to 2017, 444 outbreaks were reported within the United States alone, resulting in 7465 infections, 287 hospitalizations, and one death. The availability of such detailed epidemiological statistics was made possible by the inclusion of cryptosporidiosis in the National Outbreak Reporting System (USA), which has collected nationwide information on cryptosporidiosis since 1995 [61]. The system has been a tremendous resource for research on cryptosporidiosis risk factors, modes of transmission, and development of prevention and control programs [61]. In England and Wales, the Health Protection Agency and Infection Centers report epidemiological information and test results in a pyramidal structure to national surveillance centers to track the sources and transmission routes of cryptosporidiosis [62]. In France, the ANOFEL (French association of medical parasitologists) Cryptosporidium National Network was established in 2004. The network covers most of France and consists of 38 hospital-based parasite laboratories, and collects information on cryptosporidiosis case reports and samples, and publishes annual analyses to provide public health authorities with information on human cryptosporidiosis incidence and epidemiology [63]. In China, Feng et al. reported a cryptosporidiosis outbreak caused by possible intra-hospital infection and transmission that lasted more than 14 months (November 2007‒December 2008) in Shanghai, with up to 102 patients confirmed positive for Cryptosporidium [64]. Due to a lack of routine Cryptosporidium surveillance procedures, the initial source of the infection could not be identified [64]. Therefore, establishing and improving surveillance networks is critical for cryptosporidiosis control. We propose starting with highly suitable habitats, continuously enriching the database, updating the nodes of the surveillance network, and expanding the network to areas with moderate habitat suitability, to provide data support for early warning for Cryptosporidium outbreaks, traceability, prevention, and control.

Cryptosporidium infection was reported in 2.97% of subjects (5933/200,054) in an analysis of a 30-year period from 1987 to 2017 conducted in China [6]. Different prevalence rates of Cryptosporidium were observed in different age groups, with 2.56% in children under 5 years of age, 3.68% in adolescents, and 1.89% in adults, 6.57% in HIV-positive/AIDS patients, 4.89% in HBV-positive patients, 47.79% in cancer patients, and 24.14% among drug users [6]. Population characteristics of infection are consistent with global statistics: minors and people with dysfunctional, depressed, and compromised immune systems are the priority populations for Cryptosporidium infection, and should be the focus of surveillance efforts [4]. Cryptosporidium oocysts can contaminate drinking, recreational, and agricultural water following contact with infected humans or animals, leading to Cryptosporidium spread and transmission [65]. Therefore, detecting Cryptosporidium oocysts in water bodies has become an indicator for the assessment of water quality in many countries and regions [65]. Additionally, Cryptosporidium is among the most important foodborne parasites, and is usually transmitted through the fecal–oral route [1]. In recent years, outbreaks of foodborne Cryptosporidium have been associated with shifts in consumer dietary habits in favor of fresh produce. Since fresh produce is not sterilized or treated at high temperature, it is highly likely a vector for Cryptosporidium transmission. Cryptosporidium has been detected in foods such as fruits and vegetables in several countries globally, with an overall positivity rate of 6.0% (375/6210) [66]. Another characteristic of Cryptosporidium is its wide range of host animal species. Over 260 species, including mammals, reptiles, birds, amphibians, and fish, are potential hosts of Cryptosporidium spp., and more than 155 mammalian species are hosts of C. parvum. Cryptosporidium is adapting and evolving to infect more diverse hosts and is becoming a major zoonotic problem [67]. Vermeulen et al. calculated the global Cryptosporidium emission load from livestock and showed that approximately 3.2 × 1023 oocysts are discharged from livestock feces, with the highest contribution from cattle, followed by chicken and pigs [68]. Based on the aforementioned considerations, the One Health approach that includes the “human–animal–water–food–other interface” should be promoted in the integrated infectious disease surveillance networks to be established for cryptosporidiosis and other neglected tropical diseases [7].

In line with the One Health concept, it is necessary to develop a comprehensive public health approach encompassing “parasite–host–environment” for cryptosporidiosis prevention and control. In such a strategy, real-time detection and surveillance should be conducted, information exchange and sharing between internal and external parties should be increased, and effort should be made to improve surveillance networks and reporting systems. In addition, interdisciplinary and inter-departmental prevention and control mechanisms should be proposed to prevent, diagnose, monitor, control, treat, and protect against cryptosporidiosis over a wider scope, and to better assess the risk of cryptosporidiosis outbreaks and minimize hidden public health safety risks. Meanwhile, progress in drug development and advancement in vaccine development remain critical for the containment of this important pathogen.

Considering the paucity of relevant research, we could only conduct spatial simulations over large geographic scales based on available information on cryptosporidiosis in China, relying on climate data to explore strategies and models for cryptosporidiosis prevention and control. However, in the context of specific control options, a small geographic scale and multidimensional simulations on Cryptosporidium transmission dynamics may provide more specific suggestions. Secondly, due to the lack of research on the molecular biology of Cryptosporidium in China, it is not yet possible to analyze the spatial ecological niche relationships among different species. Considering cross-species transmission between humans and animals, studies on overlapping and separation of spatial ecological niches for Cryptosporidium isolated from different hosts may provide information that could facilitate cryptosporidiosis prediction and early warning.


The Maxent model can achieve sound results with regard to Cryptosporidium distribution prediction. In China, large areas are suitable for Cryptosporidium survival, which are mainly concentrated on the areas with high population densities. Key areas include the North China Plain, the Middle-Lower Yangtze Plain, and the Pearl River Basin. In contrast, the climate environment in the Qinghai–Tibet Plateau region is not suitable for Cryptosporidium survival and spread. In the context of future climate change, Cryptosporidium may gain more suitable habitats within China. Areas including northeastern, northwestern, and southwestern China and coastal regions require dynamic attention. Establishment of a national surveillance network in areas with suitable Cryptosporidium habitats could further elucidate the epidemiological trends and transmission patterns of cryptosporidiosis. The modelling information reported in the present study could facilitate the prevention and control of Cryptosporidium and other pathogenic intestinal protozoa.

Availability of data and materials

All the relevant data used and generated during this study are included in the manuscript.



Sample size corrected Akaike information criterion


Area under curve


Bayesian information criterion


Bioclimate analysis and prediction system


Coupled Model Intercomparison Project


Ecological niche models


Feature combination


Genetic algorithm for rule-set production


Global burden of disease study


Global climate models


Climatologies at high resolution for the earth’s land surface areas


Assessment Report 6 of Intergovernmental Panel on Climate Change


Maximum entropy


Percent contribution


Pearson correlation coefficients


Representative concentration pathways


Regularization multiplier


Receiver operating characteristic


Species distribution models


Shared socio-economic pathways


True skill statistic


World Climate Research Program


World Health Organization


  1. Liu J, Platts-Mills JA, Juma J, Kabir F, Nkeze J, Okoi C, et al. Use of quantitative molecular diagnostic methods to identify causes of diarrhoea in children: a reanalysis of the GEMS case-control study. Lancet. 2016;388(10051):1291–301.

    Article  CAS  PubMed  PubMed Central  Google Scholar 

  2. O’Donoghue PJ. Cryptosporidium and cryptosporidiosis in man and animals. Int J Parasitol. 1995;25(2):139–95.

    Article  CAS  PubMed  Google Scholar 

  3. Gururajan A, Rajkumari N, Devi U, Borah P. Cryptosporidium and waterborne outbreaks—a mini review. Trop Parasitol. 2021;11(1):11–5.

    Article  PubMed  PubMed Central  Google Scholar 

  4. Dong S, Yang Y, Wang Y, Yang D, Yang Y, Shi Y, et al. Prevalence of Cryptosporidium Infection in the global population: a systematic review and meta-analysis. Acta Parasitol. 2020;65(4):882–9.

    Article  PubMed  Google Scholar 

  5. Han F, Wang L, Wang RZ, Ge JJ, Shen JP. Investigation of cryptopsoridiosis in humans in Nanjing, China. Chin J Zoonoses. 1989;5(5):51.

    Google Scholar 

  6. Liu A, Gong B, Liu X, Shen Y, Wu Y, Zhang W, et al. A retrospective epidemiological analysis of human Cryptosporidium infection in China during the past three decades (1987–2018). PLoS Negl Trop Dis. 2020;14(3): e0008146.

    Article  PubMed  PubMed Central  Google Scholar 

  7. Yin J, Shen Y, Cao J. Burden of Cryptosporidium infections in the Yangtze River Delta in China in the 21st century: a one health perspective. Zoonoses. 2022;2(1):7.

    Article  Google Scholar 

  8. Wang X, Shen YJ, Cao JP. Epidemic status and prevention and control process of cryptosporidiosis in China. J Trop Dis Parasitol. 2022;20(3):136–48.

    CAS  Google Scholar 

  9. Sillero N, Arenas-Castro S, Enriquez-Urzelai U, Vale CG, Sousa-Guedes D, Martínez-Freiría F, et al. Want to model a species niche? A step-by-step guideline on correlative ecological niche modelling. Ecol Model. 2021;456: 109671.

    Article  Google Scholar 

  10. Barbosa MA, Sillero N, Martínez-Freiría F, Real R. Ecological niche models in mediterranean herpetology: past, present and future. In: Zhang WJ, editor. Ecological Niche Models in Mediterranean Herpetology. New York: Nova Science Publishers; 2012. p. 173–204.

    Google Scholar 

  11. Busby JR. BIOCLIM: a bioclimate analysis and prediction system. In: Margules CR, Austin MP, editors. Nature conservation: cost effective biological surveys and data analysis. Melbourne: CSIRO; 1991. p. 64–8.

    Google Scholar 

  12. Stockwell DRB. The GARP modelling system: Problems and solutions to automated spatial prediction. Int J Geogr Inf Sci. 1999;13(2):143–58.

    Article  Google Scholar 

  13. Carpenter G, Gillison AN, Winter J. DOMAIN: a flexible modelling procedure for mapping potential distributions of plants and animals. Biodivers Conserv. 1993;2(6):667–80.

    Article  Google Scholar 

  14. Phillips SJ, Anderson RP, Schapire RE. Maximum entropy modeling of species geographic distributions. Ecol Model. 2006;190:231–59.

    Article  Google Scholar 

  15. Escobar LE, Qiao H, Lee C, Phelps NBD. Novel methods in disease biogeography: a case study with heterosporosis. Front Vet Sci. 2017;4:105.

    Article  PubMed  PubMed Central  Google Scholar 

  16. Escobar LE, Craft ME. Advances and limitations of disease biogeography using ecological niche modeling. Front Microbiol. 2016;7:1174.

    Article  PubMed  PubMed Central  Google Scholar 

  17. Escobar LE, Carver S, Romero-Alvarez D, VandeWoude S, Crooks KR, Lappin MR, Craft ME. Inferring the ecological niche of Toxoplasma gondii and Bartonella spp. in wild felids. Front Vet Sci. 2017;4:172.

    Article  PubMed  PubMed Central  Google Scholar 

  18. Mirzanejad-Asl H, Karimi A, Babaei Pouya N, Moradi-Asl E. Spatio-temporal analysis and determination of the ecological niche model of Giardia Lamblia (Lambl, 1859) in Ardabil province, northwestern Iran. J Parasit Dis. 2021;45(3):706–14.

    Article  PubMed  PubMed Central  Google Scholar 

  19. Garrido R, Bacigalupo A, Peña-Gómez F, Bustamante RO, Cattan PE, Gorla DE, et al. Potential impact of climate change on the geographical distribution of two wild vectors of Chagas disease in Chile: Mepraia spinolai and Mepraia gajardoi. Parasit Vectors. 2019;12(1):478.

    Article  PubMed  PubMed Central  Google Scholar 

  20. Meshgi B, Majidi-Rad M, Hanafi-Bojd AA, Fathi S. Ecological niche modeling for predicting the habitat suitability of fascioliasis based on maximum entropy model in southern Caspian Sea littoral, Iran. Acta Trop. 2019;198: 105079.

    Article  PubMed  Google Scholar 

  21. Kuhn T, Cunze S, Kochmann J, Klimpel S. Environmental variables and definitive host distribution: a habitat suitability modelling for endohelminth parasites in the marine realm. Sci Rep. 2016;6:30246.

    Article  CAS  PubMed  PubMed Central  Google Scholar 

  22. Slater H, Michael E. Predicting the current and future potential distributions of lymphatic filariasis in Africa using maximum entropy ecological niche modelling. PLoS ONE. 2012;7(2): e32202.

    Article  CAS  PubMed  PubMed Central  Google Scholar 

  23. Escobar LE. Ecological niche modeling: an introduction for veterinarians and epidemiologists. Front Vet Sci. 2020;7: 519059.

    Article  PubMed  PubMed Central  Google Scholar 

  24. Hu WB, Mengersen K, Fu SY, Tong SL. The use of ZIP and CART to model cryptosporidiosis in relation to climatic variables. Int J Biometeorol. 2010;54(4):433–40.

    Article  PubMed  Google Scholar 

  25. Gonzalez-Moreno O, Hernandez-Aguilar RA, Piel AK, Stewart FA, Gracenea M, Moore J. Prevalence and climatic associated factors of Cryptosporidium sp. infections in savanna chimpanzees from Ugalla, Western Tanzania. Parasitol Res. 2013;112(1):393–9.

    Article  PubMed  Google Scholar 

  26. Young I, Smith BA, Fazil A. systematic review and meta-analysis of the effects of extreme weather events and other weather-related variables on Cryptosporidium and Giardia in fresh surface waters. J Water Health. 2015;13(1):1–17.

    Article  PubMed  Google Scholar 

  27. Ikiroma IA, Pollock KG. Influence of weather and climate on cryptosporidiosis-a review. Zoonoses Public Health. 2021;68(4):285–98.

    Article  PubMed  Google Scholar 

  28. Wang X, Wang X, Cao J. Environmental factors associated with Cryptosporidium and Giardia. Pathogens. 2023;12(3):420.

    Article  CAS  PubMed  PubMed Central  Google Scholar 

  29. Jagai JS, Castronovo DA, Monchak J, Naumova EN. Seasonality of cryptosporidiosis: a meta-analysis approach. Environ Res. 2009;109(4):465–78.

    Article  CAS  PubMed  PubMed Central  Google Scholar 

  30. Polley L, Thompson RC. Parasite zoonoses and climate change: molecular tools for tracking shifting boundaries. Trends Parasitol. 2009;25(6):285–91.

    Article  CAS  PubMed  Google Scholar 

  31. Rohr JR, Dobson AP, Johnson PT, Kilpatrick AM, Paull SH, Raffel TR, et al. Frontiers in climate change-disease research. Trends Ecol Evol. 2011;26(6):270–7.

    Article  PubMed  PubMed Central  Google Scholar 

  32. Carlson CJ, Burgio KR, Dougherty ER, Phillips AJ, Bueno VM, Clements CF, et al. Parasite biodiversity faces extinction and redistribution in a changing climate. Sci Adv. 2017;3(9): e1602422.

    Article  PubMed  PubMed Central  Google Scholar 

  33. Pickles RS, Thornton D, Feldman R, Marques A, Murray DL. Predicting shifts in parasite distribution with climate change: a multitrophic level approach. Glob Chang Biol. 2013;19(9):2645–54.

    Article  PubMed  Google Scholar 

  34. Hijmans RJ, Cameron SE, Parra JL, Jones PG, Jarvis A. Very high resolution interpolated climate surfaces for global land areas. Int J Climatol. 2005;25(15):1965–78.

    Article  Google Scholar 

  35. Fick SE, Hijmans RJ. WorldClim 2: new 1km spatial resolution climate surfaces for global land areas. Int J Climatol. 2017;37(12):4302–15.

    Article  Google Scholar 

  36. Karger DN, Conrad O, Böhner J, Kawohl T, Kreft H, Soria-Auza RW, et al. Climatologies at high resolution for the earth’s land surface areas. Sci Data. 2017;4: 170122.

    Article  PubMed  PubMed Central  Google Scholar 

  37. Moss RH, Edmonds JA, Hibbard KA, Manning MR, Rose SK, van Vuuren DP, et al. The next generation of scenarios for climate change research and assessment. Nature. 2010;463:747–56.

    Article  CAS  PubMed  Google Scholar 

  38. Yukimoto S, Kawai H, Koshiro T, Oshima N, Yoshida K, Urakawa SL, et al. The Meteorological Research Institute Earth System Model Version 2.0, MRI-ESM2.0: description and basic evaluation of the physical component. J Meteorol Soc JPN. 2019;97(5):931–65.

    Article  Google Scholar 

  39. Jiang Y, Yuan Z, Liu H, Yin J, Qin Y, Jiang X, et al. Intestinal protozoan infections in patients with Diarrhea—Shanghai Municipality, Zhenjiang City, and Danyang City, China, 2011–2015 and 2019–2021. China CDC Wkly. 2022;4(8):143–7.

    Article  PubMed  PubMed Central  Google Scholar 

  40. ESRI. ArcGIS Desktop: Release 10. Redlands, CA: Environmental Systems Research Institute. 2011.

  41. IMB Corp. IBM SPSS Statistics for Windows, Version 26.0. Armonk, NY: IBM Corp. 2019.

  42. Li J, Miao B, Wang S, Dong W, Xu H, Si C, et al. Hiplot: a comprehensive and easy-to-use web service for boosting the publication-ready biomedical data visualization. Brief Bioinform. 2022;23(4):bbac261.

    Article  PubMed  Google Scholar 

  43. Warren DL, Glor RE, Turelli M. ENMTools: a toolbox for comparative studies of environmental niche models. Ecography. 2010;33:607–11.

    Google Scholar 

  44. Dormann CF, Schymanski SJ, Cabral J, Chuine I, Graham C, Hartig F, et al. Correlationand process in species distribution models: bridging a dichotomy. J Biogeogr. 2012;39(12):2119–31.

    Article  Google Scholar 

  45. Sillero N. What does ecological modelling model? A proposed classification of ecological niche models based on their underlying methods. Ecol Model. 2011;222:1343–6.

    Article  Google Scholar 

  46. Phillips, S.J. and Dudík, M. Schapire RE. Maxent Software for Modeling Species Niches and Distributions (Version 3.4.1). New York: American Museum of Natural History, 2006. Accessed 30 Aug 2022.

  47. Hijmans R, Guarino L, Mathur P. DIVA-GIS version 7.5 manual. Lima: International Potato Center, 2012. Accessed 30 Aug 2022.

  48. Scachetti-Pereira R. DesktopGarp: a software package for biodiversity and ecologic research. Lawrence, Kansas: The University of Kansas Biodiversity Research Center, 2002. Accessed 30 Aug 2022.

  49. Qiao H, Peterson AT, Campbell LP, Sobern J, Ji L, Escobar LE. NicheA: creating virtual species and ecological niches in multivariate environmental scenarios. Ecography. 2016;39(8):805–13.

    Article  Google Scholar 

  50. Allouche O, Tsoar A, Kadmon R. Assessing the accuracy of species distribution models: prevalence, kappa and the true skill statistic (TSS). J Appl Ecol. 2010;43(6):1223–32.

    Article  Google Scholar 

  51. Segurado P, Araújo MB. An evaluation of methods for modelling species distributions. J Biogeogr. 2004;2004(31):1555–68.

    Article  Google Scholar 

  52. Hanley JA, Mcneil BJ. The meaning and use of the area under a receiver operating characteristic (ROC) curve. Radiology. 1982;143(1):29–36.

    Article  CAS  PubMed  Google Scholar 

  53. Warren DL, Seifert SN. Ecological niche modeling in Maxent: the importance of model complexity and the performance of model selection criteria. Ecol Appl. 2011;21(2):335–42.

    Article  PubMed  Google Scholar 

  54. Morales NS, Fernández IC, Baca-González V. MaxEnt’s parameter configuration and small samples: are we paying attention to recommendations? A systematic review. Peer J. 2017;5: e3093.

    Article  PubMed  PubMed Central  Google Scholar 

  55. Merow C, Smith M, Silander J. A practical guide to MaxEnt for modeling species’ distributions: what it does, and why inputs and settings matter. Ecography. 2013;36:1058–69.

    Article  Google Scholar 

  56. Phillips SJ, Dudík M. Modeling of species distributions with maxent: new extensions and a comprehensive evaluation. Ecography. 2008;31:161–75.

    Article  Google Scholar 

  57. Hu HY. The distribution of population in China, with statistics and maps. Acta Geogr Sin. 1935;2(2):33–74.

    Google Scholar 

  58. Brooks DR, Hoberg EP. How will global climate change affect parasite-host assemblages? Trends Parasitol. 2007;23(12):571–4.

    Article  PubMed  Google Scholar 

  59. Ajjampur SS, Liakath FB, Kannan A, Rajendran P, Sarkar R, Moses PD, et al. Multisite study of cryptosporidiosis in children with diarrhea in India. J Clin Microbiol. 2010;48(6):2075–81.

    Article  CAS  PubMed  PubMed Central  Google Scholar 

  60. Feng Y, Xiao L. Molecular epidemiology of Cryptosporidiosis in China. Front Microbiol. 2017;8:1701.

    Article  PubMed  PubMed Central  Google Scholar 

  61. Cryptosporidiosis NNDSS Summary Report for 2019. Centers for Disease Control and Prevention, Atlanta. 2021. Accessed 30 Aug 2021.

  62. Lake IR, Nichols G, Harrison FC, Bentham G, Sari Kovats R, Grundy C, et al. Using infectious intestinal disease surveillance data to explore illness aetiology; a cryptosporidiosis case study. Health Place. 2009;15(1):333–9.

    Article  PubMed  PubMed Central  Google Scholar 

  63. ANOFEL Cryptosporidium National Network. Laboratory-based surveillance for Cryptosporidium in France, 2006–2009. Euro Surveill. 2010;15(33):19642.

    Article  Google Scholar 

  64. Feng Y, Wang L, Duan L, Gomez-Puerta LA, Zhang L, Zhao X, et al. Extended outbreak of cryptosporidiosis in a pediatric hospital. China Emerg Infect Dis. 2012;18(2):312–4.

    Article  PubMed  Google Scholar 

  65. Cao SK, Jiang YY, Yuan ZY, Yin JH, Xu M, Xue JB, et al. Quantitative microbial risk assessment of Cryptosporidium and Giardia in Public Drinking Water in China. Biomed Environ Sci. 2021;34(6):493–8.

    PubMed  Google Scholar 

  66. Li J, Wang Z, Karim MR, Zhang L. Detection of human intestinal protozoan parasites in vegetables and fruits: a review. Parasit Vectors. 2020;13(1):380.

    Article  PubMed  PubMed Central  Google Scholar 

  67. Ryan U, Fayer R, Xiao L. Cryptosporidium species in humans and animals: current understanding and research needs. Parasitology. 2014;141(13):1667–85.

    Article  PubMed  Google Scholar 

  68. Vermeulen LC, Benders J, Medema G, Hofstra N. Global Cryptosporidium loads from livestock manure. Environ Sci Technol. 2017;51(15):8663–71.

    Article  CAS  PubMed  PubMed Central  Google Scholar 

Download references


We thank Xue Jingbo (National Institute of Parasitic Diseases, Chinese Center for Disease Control and Prevention) for technical support of spatial analysis. We are grateful to the Department of Infectious Diseases and the Department of Pediatrics, Shanghai Sixth People’s Hospital in Shanghai City; the Department of Clinical Laboratory, Affiliated Hospital of Jiangsu University; and the Department of Infectious Diseases, Danyang Hospital of Jiangsu Province for providing monitoring samples.


This study was supported by the National Natural Science Foundation of China (Nos. 81971969, 82272369 to JC), the Three-Year Public Health Action Plan (2020–2022) of Shanghai (No. GWV-10.1-XK13 to JC), and the Research Projects of Shanghai Municipal Health Commission (No. 2021Y0213 to XW). The funders had no role in the study design, the data collection, and analysis, the decision to publish, or the preparation of the manuscript.

Author information

Authors and Affiliations



XW, JC and YS conceived and designed the research. XW, YJ, NX and QC collected data from databases and Cryptosporidium monitoring sites. XW carried out the data analyses and wrote the paper. JC, YS, WW, XH, ZW and YG directed the study and contributed to the writing of the manuscript. All authors read and approved the final manuscript.

Corresponding authors

Correspondence to Yujuan Shen or Jianping Cao.

Ethics declarations

Ethics approval and consent to participate

The protocol used to collect patient information was approved by the Ethical Review Committee of the National Institute of Parasitic Diseases, Chinese Center for Disease (Chinese Center for Tropical Disease Research) (identification number: 2019003).

Consent for publication

Not applicable.

Competing interests

The authors declare that they have no competing interests.

Supplementary Information

Additional file 1.

Brief description of WorldClim and Climatologies at High Resolution for the Earth’s Land Surface Areas (CHELSA) database characteristics.

Additional file 2.

Study and analysis flow chart.

Additional file 3.

Maps of extracted Cryptosporidium presence data (occurrence points) in China and neighboring countries.

Additional file 4.

Reference list of reports of human infected with Cryptosporidium in China.

Additional file 5.

References for human cases of Cryptosporidium in countries neighboring China.

Additional file 6.

Combined points graph of percentage contribution (PC) and plots of Pearson Correlation Coefficients (PCCs) for 19 bioclimatic variables.

Additional file 7.

Predicted habitat suitability for Cryptosporidium based on historical data (1981‒2010). a-1) Predicted suitable habitats for Cryptosporidium. a-2) Standard deviation of prediction results (Cloglog value). b) Receiver Operating Characteristic (ROC) curves for predicted suitable habitats.

Additional file 8.

Statistics of cities with high, moderate, and low habitat suitability for human-derived Cryptosporidium in China.

Additional file 9.

Predicted habitat suitability for Cryptosporidium based on historical data of the 1971‒2100 period. a-e) Predicted results based on climate data from the WorldClim database for the 1971‒2000, 2021‒2040, 2041‒2060, 2061‒2080, and 2081–2100 periods. f-i) Predicted results based on climate data from the Climatologies at High Resolution for the Earth’s Land Surface Areas (CHELSA) database for the 1981‒2010, 2011‒2040, 2041‒2070, and 2071‒2100 periods.

Rights and permissions

Open Access This article is licensed under a Creative Commons Attribution 4.0 International License, which permits use, sharing, adaptation, distribution and reproduction in any medium or format, as long as you give appropriate credit to the original author(s) and the source, provide a link to the Creative Commons licence, and indicate if changes were made. The images or other third party material in this article are included in the article's Creative Commons licence, unless indicated otherwise in a credit line to the material. If material is not included in the article's Creative Commons licence and your intended use is not permitted by statutory regulation or exceeds the permitted use, you will need to obtain permission directly from the copyright holder. To view a copy of this licence, visit The Creative Commons Public Domain Dedication waiver ( applies to the data made available in this article, unless otherwise stated in a credit line to the data.

Reprints and permissions

About this article

Check for updates. Verify currency and authenticity via CrossMark

Cite this article

Wang, X., Jiang, Y., Wu, W. et al. Cryptosporidiosis threat under climate change in China: prediction and validation of habitat suitability and outbreak risk for human-derived Cryptosporidium based on ecological niche models. Infect Dis Poverty 12, 35 (2023).

Download citation

  • Received:

  • Accepted:

  • Published:

  • DOI: