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Considering climate change impact on the global potential geographical distribution of the invasive Argentine ant and little fire ant

Published online by Cambridge University Press:  16 May 2024

Tong Li Open the ORCID record for Tong Li [Opens in a new window] ,
Pei Jiang ,
Jingyuan Liu ,
Jingquan Zhu ,
Shouqi Zhao ,
Zhihong Li ,
Mina Zhong ,
Chen Ma  and
Yujia Qin Open the ORCID record for Yujia Qin [Opens in a new window]
Tong Li
Affiliation:
Department of Plant Biosecurity, Key Laboratory of Surveillance and Management for Plant Quarantine Pests of MARA, College of Plant Protection, China Agricultural University, Beijing, P. R. China
Pei Jiang
Affiliation:
National Agro-tech Extension and Service Center, Ministry of Agriculture and Rural Affairs, Beijing, 100125, China
Jingyuan Liu
Affiliation:
Center for Animal, Plant and Food Inspection and Quarantine of Shanghai Customs District, Shanghai, 200135, China
Jingquan Zhu
Affiliation:
National Agro-tech Extension and Service Center, Ministry of Agriculture and Rural Affairs, Beijing, 100125, China
Shouqi Zhao
Affiliation:
National Agro-tech Extension and Service Center, Ministry of Agriculture and Rural Affairs, Beijing, 100125, China
Zhihong Li
Affiliation:
Department of Plant Biosecurity, Key Laboratory of Surveillance and Management for Plant Quarantine Pests of MARA, College of Plant Protection, China Agricultural University, Beijing, P. R. China
Mina Zhong
Affiliation:
Forest Pest Control and Quarantine Station of Xining City, Qinghai, 810008, China
Chen Ma*
Affiliation:
National Agro-tech Extension and Service Center, Ministry of Agriculture and Rural Affairs, Beijing, 100125, China
Yujia Qin*
Affiliation:
Department of Plant Biosecurity, Key Laboratory of Surveillance and Management for Plant Quarantine Pests of MARA, College of Plant Protection, China Agricultural University, Beijing, P. R. China
*
Corresponding author: Yujia Qin; Email: [email protected]; Chen Ma; Email: [email protected]
Corresponding author: Yujia Qin; Email: [email protected]; Chen Ma; Email: [email protected]
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Abstract

The Argentine ant (Linepithema humile) and the little fire ant (Wasmannia auropunctata) are among the top 100 invasive alien species globally, causing significant ecological and economic harm. Therefore, it is crucial to study their potential geographic distribution worldwide. This study aimed to predict their global distribution under current and future climate conditions. We used distribution data from various sources, including CABI, GBIF, and PIAKey, and key climate variables selected from 19 environmental factors to model their potential geographic distribution using MaxEnt. The AUC values were 0.925 and 0.937 for L. humile and W. auropunctata, respectively, indicating good predictive performance. Suitable areas for L. humile were mainly in southern North America, northern South America, Europe, central Asia, southern Oceania, and parts of Africa, while W. auropunctata suitable areas were mostly in southern North America, most of South America, a small part of Europe, southern Asia, central Africa, and some parts of Oceania. Under climate change scenario, suitable areas for L. humile increased, while highly suitable areas for W. auropunctata decreased. The top four countries with the largest areas of overlapping suitable habitat under current climate were Brazil, China, Australia, and Argentina, while under future SSP585 climate scenario, the top four countries were Brazil, China, Indonesia, and Argentina. Some countries, such as Estonia and Finland, will see an overlapping adaptation area under climate change. In conclusion, this study provides insight into controlling the spread and harm of L. humile and W. auropunctata.

Keywords

climate changeLinepithema humileMaxEntPotential geographical distributionWasmannia auropunctata
Type
Research Paper
Information
Bulletin of Entomological Research , Volume 114 , Issue 3 , June 2024 , pp. 454 - 465
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Copyright
Copyright © The Author(s), 2024. Published by Cambridge University Press

Introduction

Invasive alien species (IAS) are species that have been introduced into non-native areas, where they can negatively impact local ecosystems and even pose risks to human health and safety (Pejchar and Mooney, Reference Pejchar and Mooney2009; Zhu et al., Reference Zhu, Tang, Limpanont, Wu, Li and Lv2019). The biological impacts of IAS are serious and can include increased risk of local species extinction, reduced species diversity, and altered ecosystem functions (Pysek et al., Reference Pysek, Hulme, Simberloff, Bacher, Blackburn, Carlton, Dawson, Essl, Foxcroft, Genovesi, Jeschke, Kuehn, Liebhold, Mandrak, Meyerson, Pauchard, Pergl, Roy, Seebens, van Kleunen, Vila, Wingfield and Richardson2020). Additionally, IAS can harm the agroecological economy, threatening the food security of farmers (Pratt et al., Reference Pratt, Constantine and Murphy2017). Climate is generally accepted as an important factor influencing the spread and distribution of IAS (Shi et al., Reference Shi, Luo, Zhou and He2010; Verlinden et al., Reference Verlinden, De Boeck and Nijs2014; Ar et al., Reference Ar, Tuttu, Gulcin, Ozcan, Kara, Surmen, Cicek and Velazquez2022). Therefore, studying and mapping potential habitats with the help of climate factors can aid in preventing invasion and spread, managing and monitoring current epidemic areas, and understanding the trend of range expansion and invasion (Kumar et al., Reference Kumar, LeBrun, Stohlgren, Stabach, McDonald, Oi and LaPolla2015; Lee et al., Reference Lee, Lee, Kwon, Athar and Park2021).

The Argentine ant (Linepithema humile) and the little fire ant (Wasmannia auropunctata) are both considered to be among the 100 most dangerous invasive species in the world by the Invasive Species Specialist Group (ISSG). L. humile is a highly aggressive and expansive pest that can thrive under human interference and harm ecosystems such as farmland and green spaces (Ness and Bronstein, Reference Ness and Bronstein2004; Carpintero et al., Reference Carpintero, Reyes-Lopez and De Reyna2005; Lopez-Collar and Cabrero-Sanudo, Reference Lopez-Collar and Cabrero-Sanudo2021). L. humile is native to the Paraná River drainage basin in subtropical South America (between northern Argentina, southern Brazil, Uruguay and Paraguay), and it is already widely distributed in Ecuador, Guatemala, the Dominican Republic, Jamaica, Puerto Rico, South Africa, and the western United States (Wild, Reference Wild2004; CABI Compendium, 2022a). Native to Central and South America, W. auropunctata is also aggressive and can even severely bite animals in addition to attacking other colonies (Holway et al., Reference Holway, Lach, Suarez, Tsutsui and Case2002; Wetterer and Porter, Reference Wetterer and Porter2003). And it has now spread to Cameroon, Gabon, Israel, Germany, Spain, the United Kingdom, and others (CABI Compendium, 2022b). Furthermore, its strong adaptability and competitiveness enable it to outcompete native ants and impact human health (Foucaud et al., Reference Foucaud, Orivel, Fournier, Delabie, Loiseau, Le Breton, Cerdan and Estoup2009; Bertelsmeier et al., Reference Bertelsmeier, Avril, Blight, Jourdan and Courchamp2015b). Given the invasive and destructive nature of L. humile and W. auropunctata, it is crucial to understand their potential geographic distribution.

Ecological niche models (ENMs) use current distribution data of species and related environmental variables to construct a model based on certain algorithms, projecting results into different times (past and future) and spaces to predict potential geographic distributions of species. ENMs have been widely used in recent years to predict suitable habitats for IAS, guiding decision-making for early warning, scientific prevention and control of alien species after invasion (Peterson, Reference Peterson2003; Teles et al., Reference Teles, Silva, Vilela, Lima-Junior, Pires-Oliveira and Miranda2022). Among the many models, the maximum entropy model (MaxEnt) is the most popular, widely used, and recognised for its accuracy and reliability (Warren and Seifert, Reference Warren and Seifert2011; Huercha et al., Reference Huercha, Song, Ma, Hu, Li, Li, Wu, Li, Dao, Fan, Hao and Bayin2020; Dai et al., Reference Dai, Wu, Ji, Tian, Yang, Guan and Wu2022). For example, Zhang et al. (Reference Zhang, Chen, Zhang and Li2023) used MaxEnt to predict the potential geographic distributions and overlap of Prunus salicina and Monilinia fructicola in China, while Sopniewski et al. (Reference Sopniewski, Scheele and Cardillo2022) used MaxEnt to predict the potential geographic distribution of Australian frogs under climate change and analysed their overlap with Batrachochytrium dendrobatidis.

Researches on the invasion and distribution of L. humile and W. auropunctata have been carried out respectively (Harris and Barker, Reference Harris and Barker2007; Roura-Pascual et al., Reference Roura-Pascual, Bas, Thuiller, Hui, Krug and Brotons2009; Li et al., Reference Li, Xian, Zhao, Xue, Chen, Huang, Wan and Liu2022; Mao et al., Reference Mao, Chen, Ke, Qian and Xu2022; Zhao et al., Reference Zhao, Xian, Guo, Yang, Zhang, Chen, Huang and Liu2022). The overlap areas where are both suitable habitats for L. humile and W. auropunctata may be a higher risk of their further invasion (Bertelsmeier et al., Reference Bertelsmeier, Ollier, Avril, Blight, Jourdan and Courchamp2016). Thus, this study utilises the MaxEnt model to predict the current and future global potential geographic distributions of L. humile and W. auropunctata and their overlapping distribution regions. The purpose is to provide a basis for developing appropriate prevention and control plans for these two invasive ants.

Materials and methods

Materials

The map data was downloaded from the world map of Natural Earth (https://www.naturalearthdata.com/). The distribution data of L. humile and W. auropunctata were obtained from CABI (https://www.cabi.org/isc; Gómez and Abril, Reference Gómez and Abril2022; Gunawardana and Wetterer, Reference Gunawardana and Wetterer2022), Global Biodiversity Information Facility (https://www.gbif.org/, https://doi.org/10.15468/dl.v8ap26 and https://doi.org/10.15468/dl.y56zsq, respectively) and PIAK (http://idtools.org/id/ants/pia/index.html; Sarnat, Reference Sarnat2008). Both historical and future climatic data including 19 bioclimatic variables were downloaded from the World Climate WorldClim2.1 Database (https://www.worldclim.org/). The historical climatic data covers minimum, average, and maximum temperature and precipitation from 1970 to 2000 with a spatial resolution of 5arc-min. Future climate data was in 2050 (2041–2060) come from CMIP6 BCC-CSM2-MR model, which is an atmospheric-oceanic coupled climate model developed by the Beijing Climate Center for simulating future climate change (Wu et al., Reference Wu, Lu, Fang, Xin, Li, Li, Jie, Zhang, Liu, Zhang, Zhang, Zhang, Wu, Li, Chu, Wang, Shi, Liu, Wei, Huang, Zhang and Liu2019). There are four future climate scenarios: SSP126, SSP245, SSP370, and SSP585. These scenarios represent different levels of radiative forcing and greenhouse gas emissions. From SSP126 to SSP585, greenhouse gas emissions increase progressively (O'Neill et al., Reference O'Neill, Kriegler, Ebi, Kemp-Benedict, Riahi, Rothman, van Ruijven, van Vuuren, Birkmann, Kok, Levy and Solecki2017). MaxEnt 3.4.4 was downloaded from https://biodiversityinformatics.amnh.org/open_source/maxent/. R4.1.2 was downloaded from https://cran.r-project.org/ and rstudio is downloaded from https://www.rstudio.com/. ArcGIS 10.2 purchased by Plant Quarantine and Invasion Biology Laboratory, College of Plant Protection, China Agricultural University.

Distributional data and environmental variables

The distribution data for L. humile and W. auropunctata were obtained from CABI, GBIF, and PIAKey, as shown in fig. 1. After combining the three datasets, we checked for bias in the distribution points. To reduce sampling bias, we standardised the geographical distribution data and environmental variables to the same accuracy (5 minutes) and removed duplicate data, resulting in 1309 distribution data points for L. humile and 717 distribution data points for W. auropunctata. We imported the distribution data and 19 climate variables into ArcGIS 10.2 and used the Spatial Analyst tool in the ArcToolbox to perform sampling analysis. We then imported the sampling results into IBM SPSS Statistics version 26 for factor analysis and correlation analysis. If the correlation between two climate variables was greater than 0.8, we retained the factor with the higher contribution rate in principal component analysis.

Figure 1. The distribution data of L. humile and W. auropunctata.

Maxent model parameter setting

To avoid overfitting, we adjusted the regularisation multiplier (RM) and Feature Combination (FC) parameters of the MaxEnt model for different species using the ENMeval package in R. The FC comprises five items: ‘Linear features’, ‘Quadratic features’, ‘Product features’, ‘Threshold features’ and ‘Hinge features’. Based on the FC, we set six combination forms of L, H, LQ, LQH, LQHP, and LQHPT in RStudio. For RC, we set eight levels: 0.5, 1, 1.5, 2, 2.5, 3, 3.5, and 4. We used the ‘delta.AIcc’ value to determine the desired RM and FC, which resulted in RM = 0.5 and FCs = LQHPT for L. humile and RM = 1 and FCs = LQHPT for W. auropunctata.

Additionally, we set the following parameters: 25% of the distributed data was used as the test set, and the remaining 75% was used as the training set. We conducted 10 repeat runs using the ‘Subsample’ method. The maximum number of iterations was set to 5000, a 10 percentile training presence threshold was added, and we used ‘Jackknife’ to evaluate the importance of climate variables. Finally, we saved the MaxEnt model running results in *avg.asc format and imported them into ArcGIS 10.2. We divided the suitable area into four levels (negligible risk, low risk, medium risk, and high risk), and used the natural break classification method to determine the threshold of classification.

Maxent model accuracy test

To assess the effectiveness of our models in incorporating environmental variables, we utilised receiver operating characteristic (ROC) curves and area under the curve (AUC) values as accuracy measures (Liu et al., Reference Liu, Zhang, Huang, Zhang, Mou, Qiu, Wang, Li and Zhang2022). AUC values range from 0 to 1, with higher values indicating greater precision. A score of 0.5–0.7 indicates poor predictive performance, while a value of 0.7–0.9 represents good performance (Zhang et al., Reference Zhang, Hughes, Zhao, Li and Qin2022). A value of 0.9–1.0 indicates very good performance of the model in predicting outcomes (da Silva Galdino et al., Reference da Silva Galdino, Kumar, Oliveira, Alfenas, Neven, Al-Sadi and Picanco2016).

Calculation of suitable areas for L. humile and W. auropunctata

The suitable areas of L. humile and W. auropunctata were calculated by Arcmap10.2. The MaxEnt result files were imported into the Spatial Analyst tool in ArcToolbox and reclassified. The unsuitable area is assigned 0 and the suitable area is assigned 1. The region with a value of 1 is extracted through the ‘extract by attribute’ function of the analysis tool, namely, the suitability region. Finally, the raster data of suitable areas were imported and assigned through the ‘Display partition statistics in tables’ of regional analysis in the Spatial Analyst tool. The suitable area in each administrative region was obtained.

Analysis of overlap of suitable areas for L. humile and W. auropunctata

The maxent result files of L. humile and W. auropunctata were imported into the Spatial Analyst tool in ArcToolbox for reclassification. The two reclassification results were calculated using Raster Calculator.

Result

Contribution rate of environmental variables and model evaluation

To predict the distribution range, all 19 environment variables obtained from WorldClim were tested. From these variables, the five variables that best predicted the range of species were identified. For L. humile the contribution rates of variables from high to low were ‘Mean Temperature of Coldest Quarter’ (BIO11), ‘Precipitation of Coldest Quarter’ (BIO19), ‘Max Temperature of Warmest Month’ (BIO5), ‘Precipitation of Wettest Quarter’ (BIO16), and ‘Precipitation Seasonality’ (BIO15). The contribution rates were 65.5%, 25.7%, 4.1%, 4.1%, and 0.5%, respectively. According to the Jackknife test, BIO11 and BIO19 showed higher scores under ‘with only variable’, indicating that these variables had good predictive ability; The BIO11 score was the lowest under ‘without variable’, indicating that species distribution was more affected by precipitation (fig. 2A).

Figure 2. Contribution rate of the five selected environmental variables (A, B) and model evaluation (C, D). Panel A shows the contribution rate of the environmental variables for L. humile, while panel B shows the contribution rate for W. auropunctata. Panel C and D show the model evaluation for L. humile and W. auropunctata in terms of AUC.

For W. auropunctata, the contribution rates of variables from high to low were “Temperature Annual Range” (BIO7), “Precipitation of Wettest Month” (BIO13), “Mean Temperature of Warmest Quarter” (BIO10), “Precipitation of Driest Month” (BIO14), and “Precipitation Seasonality” (BIO15). The contribution rates were 49.1%, 22.6, 14.2%, 12.8%, 1.2%, respectively. Jackknife test showed BIO7 and BIO13 had higher scores under “with only variable”, BIO7 score was the lowest under ‘without variable’ (fig. 2B).

The average AUC of 10 replicate runs was calculated separately for L. humile and W. auropunctata, resulting in an average AUC of 0.925 and 0.937, respectively. These values indicated that the prediction effect of the model is good (fig. 2C-D).

Global potential geographic distribution of L. humile and W. auropunctata under current climate conditions

Fig. 3A depicted the suitable area of L. humile under the current climate conditions (total 3498.3125 × 104 km2). Under current climate conditions, suitable areas for L. humile were identified in various regions around the world. In Asia, suitable areas were found in multiple countries, including Turkey, Egypt, Iran, India, China, and Japan. In Europe, suitable areas were found in countries such as Norway, France, Germany, and Italy. North America had suitable areas in countries such as the United States and Canada, while South America had suitable areas in countries such as Brazil and Argentina. Suitable areas were also identified in many African countries, including Morocco, Tanzania, and South Africa, as well as in parts of Oceania, such as Indonesia and Australia. Under the current climate conditions, the top ten countries with the largest suitable areas of L. humile were shown in Table 1.

Figure 3. Potential geographic distribution of L. humile and W. auropunctata under current climate conditions. Panel A shows the suitable area for L. humile, panel B shows the suitable area for W. auropunctata.

Table 1. The top 10 countries with the largest suitable areas for Linepithema humile and Wasmannia auropunctata

Fig. 3B depicted the suitable area of W. auropunctata in the current climate conditions (total 3310.1389 × 104 km2). Under current climate conditions, suitable areas for W. auropunctata are primarily located between the Tropic of Cancer and the Tropic of Capricorn. Suitable areas in Asia include regions such as the Indian subcontinent, Southeast Asia, and Japan. Suitable areas in Europe include parts of Portugal, Spain, France, the UK, Italy, Turkey, and other countries. In North America, suitable areas include countries such as the United States, Canada, and Mexico. In South America, suitable areas are found in countries such as Brazil, Argentina, and Uruguay. In Africa, suitable areas include parts of Ghana, Nigeria, Ethiopia, and other countries. Suitable areas are also identified in Oceania, including parts of Indonesia, Australia, and Papua New Guinea. Under the current climate conditions, the top ten countries with the largest suitable areas of W. auropunctata were shown in Table 1.

Potential geographic distribution of L. humile and W. auropunctata under future climate scenarios

Under the future climate scenarios, the predicted geographical distribution of L. humile in 2050 were shown in fig. 4. Under the SSP126 scenario in 2050, the suitable areas of L. humile were projected to change globally. In Asia, the suitable area of L. humile was expected to expand, with new suitable areas appearing in places like Hokkaido in Japan, Qingdao in China, New Delhi in India, and Armenia. However, suitable areas were predicted to disappear in Riyadh in Saudi Arabia, Oman, and parts of India. In Europe, the suitable areas of L. humile were projected to expand to cover almost all of central and southern Europe. In North America, the suitable areas of L. humile were expected to expand, with new suitable areas appearing in places such as Seward in the United States and Halifax in Canada. In South America, the suitable area of L. humile was also projected to expand, with new suitable areas appearing in Suriname, Fontiboa in Brazil, Arica in Colombia, and eastern Guyana. In Africa, the suitable area of L. humile was expected to change little, with contractions in both northern and southern Africa in suitable areas, such as Algeria, Libya, and Egypt. However, suitable areas appeared in some parts of central Africa, such as the border of Cameroon, Gabon, and Congo. In Oceania, the suitable areas of L. humile were projected to slightly expand.

Figure 4. Potential geographical distribution of L. humile under four future climate scenarios. A-D showed the potential geographical distribution of L. humile in 2050 under the scenarios SSP126, SSP245, SSP370, and SSP585, respectively.

Under the SSP245 scenario in 2050, in Asia, the suitable areas of L. humile were expected to expand, with new suitable areas emerging in central Uzbekistan, New Delhi in India, Yantai in China, Hokkaido in Japan, and Palembang in Indonesia. Highly suitable areas in countries such as China, Japan, Nepal, and Pakistan were also predicted to expand. In Europe, the suitable area of L. humile was projected to expand to cover most of Europe, with highly suitable areas expanding from west to east. In North America, the suitable areas of L. humile were predicted to expand from south to north, with the suitable areas in the United States spreading to the middle, but highly suitable areas shrinking slightly. In South America, the suitable areas of L. humile were expected to expand, with new suitable areas appearing in Suriname and French Guiana. However, highly suitable areas in Argentina, Brazil, and Paraguay were projected to contract southward. In Africa, the suitable areas of L. humile were projected to change little, with suitable areas in South Sudan expanding, while those near Uganda and Rwanda shrinking. In Oceania, the suitable areas of L. humile changed little, with the suitable areas in eastern Australia expanding towards the central part.

Compared with the current climate in the SSP370 scenario in 2050, the changes in the suitable areas of L. humile were as follows: In Asia, the suitable area of L. humile expanded. Suitable areas in Uzbekistan moved northward, and suitable areas in Iran, Afghanistan, Indonesia and Pakistan expanded slightly around them. Highly suitable areas in China expanded significantly, while suitable areas in central India disappeared. In Europe, the suitable areas of L. humile expanded northward from Poland, Romania, Bulgaria and Ukraine to Moscow in Russia, southern Finland and southern Sweden. The highly suitable areas in Spain and France moved north. In North America, the suitable areas of L. humile expanded. The suitable areas in the United States expanded from the edge to the centre, and the suitable areas near Boston expanded to the northeast. The suitable areas appeared near Merida, Mexico. In South America, the suitable areas of L. humile expanded. Suitable areas appeared in northern parts of South America, such as Brazil, Peru and Colombia, Suriname and French Guiana. In Africa, the suitable areas of L. humile varied little. Suitable areas in northern Africa shrunk northward. In central Africa, suitable areas expanded around Ghana, Togo and Benin, while suitable areas shrunk in South Sudan and Ethiopia. In Oceania, the suitable areas of L. humile increased slightly. The suitable areas in northern Oceania expanded to the periphery.

Under the SSP585 scenario in 2050, in Asia, the suitable areas of L. humile increased, but highly suitable areas decreased. Suitable areas disappeared in northern India but appeared near Sri Lanka. Suitable areas in China expanded northward but highly suitable areas shrunk. Suitable areas around Indonesia and Malaysia expanded slightly. In Europe, the suitable areas of L. humile expanded, with central suitable areas extending further northeast and suitable areas around France and Spain moving further north. In North America, the suitable areas of L. humile expanded, but highly suitable areas decreased, with suitable areas spreading to the middle and suitable areas in Boston expanding northeast to St. Johns, Canada. In South America, the suitable areas of L. humile expanded, but highly suitable areas shrunk, with new suitable areas emerging in places such as Suriname, French Guiana, and western Brazil, and highly suitable areas in southeastern South America shrinking. In Africa, the suitable areas of L. humile decreased, with suitable areas in northern and southern Africa shrinking, and suitable areas around Ghana, Benin, and Togo expanding slightly. In Oceania, the suitable areas of L. humile varied greatly, with suitable areas in northern Oceania expanding, while the suitable areas in Australia shrunk to the south.

Under the future climate scenarios, the predicted geographical distribution of W. auropunctata in 2050 were shown in fig. 5. Under the SSP126 scenario in 2050, in Asia, the suitable areas of W. auropunctata tended to move toward south, with suitable areas in China, Myanmar, Thailand, and India decreasing, while highly suitable areas around Malaysia and Indonesia expanded. In Europe, the suitable areas of W. auropunctata increased slightly, spreading eastward from Western Europe, while highly suitable areas in Portugal, Spain, and France expanded to the periphery. In North America, the suitable areas of W. auropunctata varied little. In South America, the suitable areas of W. auropunctata decreased slightly, mainly due to the contraction of highly suitable areas and the appearance of hollow zones in some suitable areas, such as the border between Colombia and Venezuela and northeastern Brazil. In Africa, the suitable areas of W. auropunctata changed little, with suitable areas around Togo and Ghana shrinking. In Oceania, the suitable areas of W. auropunctata expanded, with highly suitable areas in Indonesia, Papua New Guinea, and New Zealand expanding to the periphery.

Figure 5. Potential geographical distribution of W. auropunctata under four future climate scenarios: SSP126, SSP245, SSP370, and SSP585 (A–D).

Under the SSP245 scenario in 2050, in Asia, suitable areas in China, Myanmar, Thailand, and India shrunk but moved northward, while highly suitable areas near Malaysia and Indonesia expanded to the periphery. In Europe, the suitable areas of W. auropunctata moved north. In North America, the suitable areas of W. auropunctata decreased slightly, with highly suitable areas shrinking in southern Mexico and the southeastern United States, while suitable areas in the northwestern United States expanded slightly. In South America, the suitable areas of W. auropunctata decreased slightly, mainly due to the shrinkage of highly suitable areas and the appearance of hollow zones, with highly suitable areas in northern Brazil disappearing. In Africa, the suitable areas of W. auropunctata changed little. In Oceania, the suitable areas of W. auropunctata increased slightly, with areas such as northern Australia and southern New Zealand appearing.

Under the SSP370 scenario in 2050. In Asia, the suitable areas of W. auropunctata decreased, with suitable areas declining in southern Vietnam, India, Myanmar, Thailand, and southern China, while suitable areas around Malaysia and Indonesia expanded. In Europe, the suitable areas of W. auropunctata moved northward, with suitable areas appearing in places such as Lithuania, northern Ukraine, and Sweden. In North America, the suitable areas of W. auropunctata decreased, with the suitable areas in the southeastern United States and southern Mexico shrinking to the south, and highly suitable areas decreasing. In South America, a large number of suitable areas of W. auropunctata disappeared or shrunk, such as central Brazil, Venezuela, Colombia, and northern Paraguay. In Africa, the suitable areas of W. auropunctata decreased slightly, but the highly suitable areas expanded around it. In Oceania, the suitable areas of W. auropunctata changed little, with the suitable areas in Australia shrinking slightly, such as the disappearance of the suitable area in the north, while the suitable areas in New Zealand expanded slightly.

Under the SSP585 scenario in 2050, in Asia, the suitable areas of W. auropunctata decreased, with highly suitable areas in southern China almost disappearing. In Europe, the suitable areas of W. auropunctata moved northwest, with Ireland and the UK mostly covered by suitable areas, while suitable areas in eastern France disappeared, but appeared in Sweden and southern Norway. In North America, the suitable areas of W. auropunctata decreased, with suitable areas in the southeastern United States and southern Mexico shrinking, but suitable areas in the northwestern United States expanding northward. In South America, the suitable areas of W. auropunctata reduced, with a large number of gaps, such as Venezuela, central Brazil, Bolivia, and Paraguay. In Africa, the suitable areas of W. auropunctata decreased, but the highly suitable areas were more concentrated, with suitable areas shrinking in places such as South Sudan, Ghana, Togo, and Zambia, but highly suitable areas more concentrated near the Democratic Republic of Congo. In Oceania, the suitable areas of W. auropunctata changed little, with the suitable area of northwest Australia disappearing, but the suitable areas of southern New Zealand appearing.

Changes in the overlap of potential geographical distribution of L. humile and W. auropunctata under climate change

Fig. 6A showed the overlap of suitable areas of L. humile and W. auropunctata under the current climate conditions (total 1539.0625 × 104 km2). The overlap of suitable areas for both L. humile and W. auropunctata under current climate conditions was identified in various regions around the world. In Asia, suitable areas were found in countries such as Nepal, India, and Indonesia. In Europe, suitable areas were identified in parts of Portugal, Spain, France, and other countries. North America had suitable areas in countries such as the United States and Mexico, while South America had suitable areas in countries such as Brazil and Argentina. Suitable areas were also identified in many African countries, such as Ethiopia and Madagascar, as well as in parts of Oceania, including Australia and New Zealand.

Figure 6. The overlap areas of potential geographic distributions of L. humile and W. auropunctata under current (A) and future SSP585 climate scenario (B).

Under the SSP585 scenario, the overlapping potential geographical distribution of L. humile and W. auropunctata in 2050 was shown in fig. 6B. Compared to the overlap areas of potential distribution under current climate conditions, the results showed that with the climate change, the global suitable overlap areas of L. humile and W. auropunctata increased from 1539.0625 × 104 km2 to 1579.9028 × 104 km2, representing a 2.65% increase or a difference of 40.8403 × 104 km2. The top ten countries with the largest increase overlap suitable areas were shown in Table 2.

Table 2. Top ten countries with the largest expansion of suitable overlap areas of L. humile and W. auropunctata under the SSP585 climate change scenario, including percentage increase

With climate change, overlap suitable areas emerged in some countries such as Latvia, Estonia, Finland, Aland, Afghanistan, Barbados, Saint Pierre, and Miquelon, Singapore and Grenada. There were also some countries that used to have overlapping suitable areas disappeared with climate change, such as Aruba, Bulgaria, Jordan, Guinea, Burkina Faso, and Zambia.

Discussion

This study presented a unique contribution by concurrently examining the potential geographical distribution and overlap suitable areas for both L. humile and W. auropunctata utilising the MaxEnt model. While previous studies have individually explored these two species using the MaxEnt or other SDM models, this is the first investigation to compare them side by side and assess their overlapping areas (Jung et al., Reference Jung, Kim, Jung and Lee2022; Li et al., Reference Li, Xian, Zhao, Xue, Chen, Huang, Wan and Liu2022; Mao et al., Reference Mao, Chen, Ke, Qian and Xu2022).

Environmental variables

In this study, five key environmental variables were screened for L. humile, and it was found that the two factors that most affect L. humile were ‘Mean Temperature of Coldest Quarter’ and ‘Precipitation of Coldest Quarter’. This result indicated that L. humile is highly sensitive to cold temperature and humidity which is consistent with previous research findings. For example, Krushelnycky et al., Reference Krushelnycky, Joe, Medeiros, Daehler and Loope2005 found that the invasion of L. humile in low-altitude regions is limited by rainfall and temperature, while in high-altitude regions, it is influenced by elevation and temperature. (Krushelnycky et al., Reference Krushelnycky, Joe, Medeiros, Daehler and Loope2005) Schilman et al., Reference Schilman, Lighton and Holway2007 also highlighted that in the invaded region of southern California, L. humile is influenced by water-loss rates and critical water content, resulting in shorter survival time compared to native ants. This further confirms that humidity is one of the key climatic variables affecting the survival of L. humile (Schilman et al., Reference Schilman, Lighton and Holway2007). There have also been studies indicating that temperature has a significant impact on L. humile (Jumbam et al., Reference Jumbam, Jackson, Terblanche, McGeoch and Chown2008; Brightwell et al., Reference Brightwell, Labadie and Silverman2010). Jung et al., Reference Jung, Kim, Jung and Lee2022 discovered that the factors limiting the occurrence frequency of L. humile are the monthly average maximum temperature, monthly average minimum temperature, and monthly precipitation. Additionally, the occurrence of L. humile is associated with the lowest temperatures. (Jung et al., Reference Jung, Kim, Jung and Lee2022).

For W. auropunctata, five important variables were screened, and the variable with the highest influence on its distribution was ‘Temperature Annual Range’, which contributed to 49.1% of the variation. This finding is consistent with previous studies that have shown temperature as a key factor affecting the distribution of W. auropunctata (Vonshak et al., Reference Vonshak, Dayan, Ionescu-Hirsh, Freidberg and Hefetz2010; Calcaterra et al., Reference Calcaterra, Cabrera and Briano2016). Moreover, according to the findings of Chifflet et al., Reference Chifflet, Rodriguero, Calcaterra, Rey, Dinghi, Baccaro, Souza, Follett and Confalonieri2016, temperature is likely an important factor contributing to the differentiation of the two clades within the native distribution range of W. auropunctata. Additionally, temperature may impose limitations on the distribution range of W. auropunctata, allowing only the subtype adapted to colder climates to expand further south (Chifflet et al., Reference Chifflet, Rodriguero, Calcaterra, Rey, Dinghi, Baccaro, Souza, Follett and Confalonieri2016). Similarly, Coulin et al., Reference Coulin, de la Vega, Chifflet, Calcaterra and Schilman2019 correlated the thermal tolerance of W. auropunctata with the minimum temperature of the coldest month, explaining the southernmost limit of its native distribution and its physiological capacity to expand in the Mediterranean region (Coulin et al., Reference Coulin, de la Vega, Chifflet, Calcaterra and Schilman2019). However, the variables considered in this study were not sufficient, soil status, geomorphology and topography, water resources, impact of human activities, interspecific competition and other limited factors were not included (Zhao et al., Reference Zhao, Chu, He, Tang, Song and Zhu2020; Geng et al., Reference Geng, Li, Sun, Li, Zhang, Chang, Rong, Liu, Shao, Liu, Zhu, Lou, Wang and Zhang2022). Considering these variables in future studies could improve the accuracy and effectiveness of the research, as ‘overcomplicating’ the model may be better than ‘not complicating enough’ (Warren and Seifert, Reference Warren and Seifert2011; Li and Ding, Reference Li and Ding2016; Bradie and Leung, Reference Bradie and Leung2017).

Potential geographic distribution under climate change

By comparing our results with previous predictions (Li et al., Reference Li, Xian, Zhao, Xue, Chen, Huang, Wan and Liu2022; Mao et al., Reference Mao, Chen, Ke, Qian and Xu2022), we have predicted a wider range of potential distribution due to the differences from the selected environmental factors (Li and Ding, Reference Li and Ding2016). It was found that the potential distribution area of L. humile is larger than that of W. auropunctata. Given the strong colonisation ability of both L. humile and W. auropunctata, these two species will invade new habitats whenever they have the opportunity (Vogel et al., Reference Vogel, Pedersen, Giraud, Krieger and Keller2010; Calcaterra et al., Reference Calcaterra, Cabrera and Briano2016).

Under climate change, the suitable areas for L. humile were expected to increase, but the highly suitable areas will decrease. Global warming may allow L. humile to invade areas that were once unsuitable due to cold weather (Nelson et al., Reference Nelson, MacArthur-Waltz and Gordon2023). Conversely, with the changing climate, the suitable areas for W. auropunctata in the world will decline. This could be good news for urban ecosystems where W. auropunctata invasion leads to reduced species richness (Mbenoun Masse et al., Reference Mbenoun Masse, Tindo, Djieto-Lordon, Mony and Kenne2019).

In terms of land area, the suitable region for L. humile was expected to increase with climate change, while the suitable region for W. auropunctata is expected to decrease, leading to a slight reduction in the overlapping suitable areas for the two species. However, under specific climate scenarios, the suitable area for L. humile reaches its maximum under the SSP245 scenario (4119.1111 × 104 km2), while the suitable area for W. auropunctata reaches its minimum under the SSP370 scenario (2778.5347 × 104 km2). In terms of regional distribution, the temperate suitable area for L. humile will expand with climate change, while the changes in tropical suitable areas are relatively small. However, there is no clear similar trend for W. auropuncta.

Control measure suggestions for L. humile and W. auropunctata

This study identified areas where L. humile and W. auropunctata may overlap in their suitable habitats under current and future climate conditions. This information provided a basis for prevention, control, and monitoring of these two invasive ant species. Both species have negative impacts on local ant species during invasions, and they can also form mutualistic relationships with some honeydew-producing insects (Krushelnycky and Gillespie, Reference Krushelnycky and Gillespie2008; Helms, Reference Helms2013). Furthermore, when facing common enemies, they may exhibit a degree of inter-specific collaboration, which could increase their invasion success rate (Bertelsmeier et al., Reference Bertelsmeier, Ollier, Avril, Blight, Jourdan and Courchamp2016). Therefore, in areas where their suitable habitats overlap, there will be a high probability for both ant species to successfully invade.

Argentine ants exhibit a high level of sociability and cooperation, and can form super colonies through recruitment and trail-marking behaviours (Sanders and Suarez, Reference Sanders and Suarez2011; Silverman and Buczkowski, Reference Silverman and Buczkowski2016). Little fire ants, on the other hand, demonstrate strong aggression and predation behaviours, which enables them to compete for resources and establish new nests through attacking and raiding (Montgomery et al., Reference Montgomery, Vanderwoude, Lintermans and Lynch2022). In the wild, there may not be a single invasive species, but rather different species occupying different areas (Bertelsmeier et al., Reference Bertelsmeier, Avril, Blight, Confais, Diez, Jourdan, Orivel, St Germes and Courchamp2015a, Reference Bertelsmeier, Avril, Blight, Jourdan and Courchamp2015b). Therefore, ecological and biological perspectives should be considered to prevent the invasion of these ants (Walters and Mackay, Reference Walters and Mackay2005). Strategies for their prevention should be carefully considered to prevent excessive administrative costs or economic losses caused by invasive species (Lee et al., Reference Lee, Motoki, Vanderwoude, Nakamoto and Leung2015; Cuthbert et al., Reference Cuthbert, Diagne, Haubrock, Turbelin and Courchamp2022).

Chemical methods were often used to prevent them (Ellis et al., Reference Ellis, Benson, Zungoli and Bridges2008; Souza et al., Reference Souza, Follett, Price and Stacy2008; Hara et al., Reference Hara, Cabral, Niino-Duponte, Jacobsen and Onuma2011). However, in some cases, pesticides can be counterproductive to managing and eliminating invasive ants (Lester and Gruber, Reference Lester and Gruber2016). Old pest management is costly, and chemical control can be harmful to the land (Cuthbert et al., Reference Cuthbert, Diagne, Haubrock, Turbelin and Courchamp2022; Kumari et al., Reference Kumari, Jasrotia, Kumar, Kashyap, Kumar, Mishra, Kumar and Singh2022). From a biological perspective, intensifying interspecific resource competition and using pheromones to interfere with ant foraging and nesting may have unexpected effects (Mothapo and Wossler, Reference Mothapo and Wossler2014; Suiter et al., Reference Suiter, Gochnour, Holloway and Vail2021). Strengthening the research on the biological behaviour of pests will also help to reveal the secrets of their invasion (Sanmartin-Villar et al., Reference Sanmartin-Villar, Csata and Jeanson2021).

In actual production, both chemical and biological control methods have their own advantages, and plans should be made based on practical considerations (Huang et al., Reference Huang, Luo and Li2022). Quarantine is the best way to control L. humile and W. auropunctata, as it involves stopping them in the path of transmission (Suhr et al., Reference Suhr, O'Dowd, Suarez, Cassey, Wittmann, Ross and Cope2019; Si-qi et al., Reference Si-qi, Yi, Yong-yue, Hao and Yi-juan2022) and finding effective quarantine treatment measures (Follett et al., Reference Follett, Porcel and Calcaterra2016). Monitoring in the potential distribution areas of these two species will help with early warning and prevention of their invasion.

Data availability statement

The data that support the findings of this study are available in Zenodo at https://do.org/10.5281/zenodo.7678538.

Acknowledgements

We thank Ma Yu for the primary data processing and all members of the Plant Quarantine and Invasion Biology Laboratory of China Agricultural University (CAUPQL) for their comments and support. This work was supported by the Beijing Natural Science Foundation (6232023) and earmarked fund for China Agriculture Research System (CARS-02-32).

Author contribution

T. L., C. M. and Y. Q. conceived and designed the research. T. L., Y. Q. analysed the data and wrote the first draft. T. L., Z. L., J. Z., S. Z., C. M. and Y. Q. discussed the idea and reviewed the draft. T. L., J. L., P. J., M. Z., Y. Q. modified the revision manuscript. All authors revised the manuscript and approved the final version.

Competing interests

None.

References

Ar, B, Tuttu, G, Gulcin, D, Ozcan, AU, Kara, E, Surmen, M, Cicek, K and Velazquez, J (2022) Response of an invasive plant species (Cynanchum acutum L.) to changing climate conditions and its impact on agricultural landscapes. Land 11, 1438.10.3390/land11091438CrossRefGoogle Scholar
Bertelsmeier, C, Avril, A, Blight, O, Confais, A, Diez, L, Jourdan, H, Orivel, J, St Germes, N and Courchamp, F (2015a) Different behavioural strategies among seven highly invasive ant species. Biological Invasions 17, 2491–2503.10.1007/s10530-015-0892-5CrossRefGoogle Scholar
Bertelsmeier, C, Avril, A, Blight, O, Jourdan, H and Courchamp, F (2015b) Discovery-dominance trade-off among widespread invasive ant species. Ecology and Evolution 5, 2673–2683.10.1002/ece3.1542CrossRefGoogle ScholarPubMed
Bertelsmeier, C, Ollier, S, Avril, A, Blight, O, Jourdan, H and Courchamp, F (2016) Colony-colony interactions between highly invasive ants. Basic and Applied Ecology 17, 106–114.10.1016/j.baae.2015.09.005CrossRefGoogle Scholar
Bradie, J and Leung, B (2017) A quantitative synthesis of the importance of variables used in MaxEnt species distribution models. Journal of Biogeography 44, 1344–1361.10.1111/jbi.12894CrossRefGoogle Scholar
Brightwell, RJ, Labadie, PE and Silverman, J (2010) Northward expansion of the invasive Linepithema humile (Hymenoptera: Formicidae) in the Eastern United States is constrained by winter soil temperatures. Environmental Entomology 39, 1659–1665.10.1603/EN09345CrossRefGoogle ScholarPubMed
CABI Compendium (2022a) Cabicompendium.30839, doi: 10.1079/cabicompendium.30839, CABI International, Linepithema humile (Argentine ant).Google Scholar
CABI Compendium (2022b) Cabicompendium.56704, doi: 10.1079/cabicompendium.56704, CABI International, Wasmannia auropunctata (little fire ant).Google Scholar
Calcaterra, L, Cabrera, S and Briano, J (2016) Local co-occurrence of several highly invasive ants in their native range: are they all ecologically dominant species? Insectes Sociaux 63, 407–419.10.1007/s00040-016-0481-3CrossRefGoogle Scholar
Carpintero, S, Reyes-Lopez, J and De Reyna, LA (2005) Impact of Argentine ants (Linepithema humile) on an arboreal ant community in Donana National Park, Spain. Biodiversity and Conservation 14, 151–163.10.1007/s10531-005-3947-6CrossRefGoogle Scholar
Chifflet, L, Rodriguero, MS, Calcaterra, LA, Rey, O, Dinghi, PA, Baccaro, FB, Souza, JLP, Follett, P and Confalonieri, VA (2016) Evolutionary history of the little fire ant Wasmannia auropunctata before global invasion: inferring dispersal patterns, niche requirements and past and present distribution within its native range. Journal of Evolutionary Biology 29, 790–809.10.1111/jeb.12827CrossRefGoogle ScholarPubMed
Coulin, C, de la Vega, GJ, Chifflet, L, Calcaterra, LA and Schilman, PE (2019) Linking thermo-tolerances of the highly invasive ant, Wasmannia auropunctata, to its current and potential distribution. Biological Invasions 21, 3491–3504.10.1007/s10530-019-02063-0CrossRefGoogle Scholar
Cuthbert, RN, Diagne, C, Haubrock, PJ, Turbelin, AJ and Courchamp, F (2022) Are the ‘100 of the world's worst’ invasive species also the costliest? Biological Invasions 24, 1895–1904.10.1007/s10530-021-02568-7CrossRefGoogle Scholar
Dai, X, Wu, W, Ji, L, Tian, S, Yang, B, Guan, B and Wu, D (2022) MaxEnt model-based prediction of potential distributions of Parnassia wightiana (Celastraceae) in China. Biodiversity Data Journal 10, e81073.10.3897/BDJ.10.e81073CrossRefGoogle Scholar
da Silva Galdino, TV, Kumar, S, Oliveira, LSS, Alfenas, AC, Neven, LG, Al-Sadi, AM and Picanco, MC (2016). Mapping global potential risk of mango sudden decline disease caused by Ceratocystis fimbriata. Plos One 11, e0159450.10.1371/journal.pone.0159450CrossRefGoogle Scholar
Ellis, BR, Benson, EP, Zungoli, PA and Bridges, WC (2008) Evaluation of chemical control strategies for Linepithema humile (Mayr) (Hymenoptera: Formicidae) in South Carolina State Park Campgrounds. Journal of Agricultural and Urban Entomology 25, 223–232.10.3954/1523-5475-25.4.223CrossRefGoogle Scholar
Follett, PA, Porcel, S and Calcaterra, LA (2016) Effect of irradiation on queen survivorship and reproduction in the invasive fire ant Solenopsis invicta (Hymenoptera: Formicidae) and a proposed phytosanitary irradiation treatment for ants. Journal of Economic Entomology 109, 2348–2354.10.1093/jee/tow207CrossRefGoogle Scholar
Foucaud, J, Orivel, J, Fournier, D, Delabie, JHC, Loiseau, A, Le Breton, J, Cerdan, P and Estoup, A (2009) Reproductive system, social organization, human disturbance and ecological dominance in native populations of the little fire ant, Wasmannia auropunctata. Molecular Ecology 18, 5059–5073.10.1111/j.1365-294X.2009.04440.xCrossRefGoogle ScholarPubMed
Geng, W, Li, Y, Sun, D, Li, B, Zhang, P, Chang, H, Rong, T, Liu, Y, Shao, J, Liu, Z, Zhu, H, Lou, Y, Wang, Q and Zhang, J (2022) Prediction of the potential geographical distribution of Betula platyphylla Suk. in China under climate change scenarios. PloS one 17, e0262540.10.1371/journal.pone.0262540CrossRefGoogle Scholar
Gómez, C and Abril, S (2022) ‘Linepithema humile (Argentine ant)’, CABI Compendium. CABI International. Retrieved from https://doi.org/10.1079/cabicompendium.30839CrossRefGoogle Scholar
Gunawardana, D and Wetterer, JK (2022) ‘Wasmannia auropunctata (little fire ant)’, CABI Compendium. CABI International. Retrieved from https://doi.org/10.1079/cabicompendium.56704CrossRefGoogle Scholar
Hara, AH, Cabral, SK, Niino-Duponte, RY, Jacobsen, CM and Onuma, K (2011) Bait insecticides and hot water drenches against the little fire Ant, Wasmannia Auropunctata (hymenoptera: Formicidae), infesting containerized nursery plants. Florida Entomologist 94, 517–526.10.1653/024.094.0316CrossRefGoogle Scholar
Harris, RJ and Barker, G (2007) Relative risk of invasive ants (Hymenoptera: Formicidae) establishing in New Zealand. New Zealand Journal of Zoology 34, 161–178.10.1080/03014220709510075CrossRefGoogle Scholar
Helms, KR (2013) Mutualisms between ants (Hymenoptera: Formicidae) and honeydew-producing insects: are they important in ant invasions. Myrmecological News 18, 61–71.Google Scholar
Holway, DA, Lach, L, Suarez, AV, Tsutsui, ND and Case, TJ (2002) The causes and consequences of ant invasions. Annual Review of Ecology and Systematics 33, 181–233.10.1146/annurev.ecolsys.33.010802.150444CrossRefGoogle Scholar
Huang, Y, Luo, X and Li, Z (2022) Substitution or complementarity: why do rice farmers use a mix of biopesticides and chemical pesticides in China? Pest Management Science 78, 1630–1639.10.1002/ps.6781CrossRefGoogle ScholarPubMed
Huercha, , Song, R, Ma, Y, Hu, Z, Li, Y, Li, M, Wu, L, Li, C, Dao, E, Fan, X, Hao, Y and Bayin, C (2020). MaxEnt modeling of Dermacentor marginatus (Acari: Ixodidae) distribution in Xinjiang, China. Journal of Medical Entomology 57, 1659–1667.10.1093/jme/tjaa063CrossRefGoogle Scholar
Jumbam, KR, Jackson, S, Terblanche, JS, McGeoch, MA and Chown, SL (2008) Acclimation effects on critical and lethal thermal limits of workers of the Argentine ant, Linepithema humile. Journal of Insect Physiology 54, 1008–1014.10.1016/j.jinsphys.2008.03.011CrossRefGoogle ScholarPubMed
Jung, JM, Kim, SH, Jung, S and Lee, WH (2022) Spatial and climatic analyses for predicting potential distribution of an invasive ant, Linepithema humile (Hymenoptera: Formicidae). Entomological Science 25, e12527.10.1111/ens.12527CrossRefGoogle Scholar
Krushelnycky, PD and Gillespie, RG (2008) Compositional and functional stability of arthropod communities in the face of ant invasions. Ecological Applications 18, 1547–1562.10.1890/07-1293.1CrossRefGoogle ScholarPubMed
Krushelnycky, PD, Joe, SM, Medeiros, AC, Daehler, CC and Loope, LL (2005) The role of abiotic conditions in shaping the long-term patterns of a high-elevation Argentine ant invasion. Diversity and Distributions 11, 319–331.10.1111/j.1366-9516.2005.00151.xCrossRefGoogle Scholar
Kumar, S, LeBrun, EG, Stohlgren, TJ, Stabach, JA, McDonald, DL, Oi, DH and LaPolla, JS (2015) Evidence of niche shift and global invasion potential of the Tawny Crazy ant, Nylanderia fulva. Ecology and Evolution 5, 4628–4641.10.1002/ece3.1737CrossRefGoogle ScholarPubMed
Kumari, P, Jasrotia, P, Kumar, D, Kashyap, PL, Kumar, S, Mishra, CN, Kumar, S and Singh, GP (2022) Biotechnological approaches for host plant resistance to insect pests. Frontiers in Genetics 13, 914029.10.3389/fgene.2022.914029CrossRefGoogle ScholarPubMed
Lee, DJ, Motoki, M, Vanderwoude, C, Nakamoto, ST and Leung, P (2015) Taking the sting out of little fire ant in Hawaii. Ecological Economics 111, 100–110.10.1016/j.ecolecon.2015.01.010CrossRefGoogle Scholar
Lee, CM, Lee, D-S, Kwon, T-S, Athar, M and Park, Y-S (2021) Predicting the global distribution of Solenopsis geminata (Hymenoptera: Formicidae) under climate change using the MaxEnt model. Insects 12, 229.10.3390/insects12030229CrossRefGoogle ScholarPubMed
Lester, PJ and Gruber, MAM (2016) Booms, busts and population collapses in invasive ants. Biological Invasions 18, 3091–3101.10.1007/s10530-016-1214-2CrossRefGoogle Scholar
Li, Y and Ding, C (2016) Effects of sample size, sample accuracy and environmental variables on predictive performance of MaxEnt model. Polish Journal of Ecology 64, 303–312.10.3161/15052249PJE2016.64.3.001CrossRefGoogle Scholar
Li, M, Xian, X, Zhao, H, Xue, L, Chen, B, Huang, H, Wan, F and Liu, W (2022) Predicting the potential suitable area of the invasive Ant Linepithema humile in China under future climatic scenarios based on optimized MaxEnt. Diversity-Basel 14, 921.10.3390/d14110921CrossRefGoogle Scholar
Liu, L, Zhang, Y, Huang, Y, Zhang, J, Mou, Q, Qiu, J, Wang, R, Li, Y and Zhang, D (2022) Simulation of potential suitable distribution of original species of Fritillariae Cirrhosae Bulbus in China under climate change scenarios. Environmental Science and Pollution Research 29, 22237–22250.10.1007/s11356-021-17338-0CrossRefGoogle Scholar
Lopez-Collar, D and Cabrero-Sanudo, FJ (2021) Update on the invasion status of the Argentine ant, Linepithema humile (Mayr, 1868), in Madrid, a large city in the interior of the Iberian Peninsula. Journal of Hymenoptera Research 85, 161–177.10.3897/jhr.85.65725CrossRefGoogle Scholar
Mao, M, Chen, S, Ke, Z, Qian, Z and Xu, Y (2022) Using MaxEnt to predict the potential distribution of the little fire ant (Wasmannia auropunctata) in China. Insects 13, 1008.10.3390/insects13111008CrossRefGoogle ScholarPubMed
Mbenoun Masse, PS, Tindo, M, Djieto-Lordon, C, Mony, R and Kenne, M (2019). Diversity of ant assemblages (Hymenoptera: Formicidae) in an urban environment in Cameroon during and after colonization of the area by Wasmannia auropunctata. European Journal of Entomology 116, 461–467.10.14411/eje.2019.047CrossRefGoogle Scholar
Montgomery, MP, Vanderwoude, C, Lintermans, M and Lynch, AJ (2022) The little fire ant (Hymenoptera: Formicidae): a global perspective. Annals of the Entomological Society of America 115, 427–448.10.1093/aesa/saac016CrossRefGoogle Scholar
Mothapo, NP and Wossler, TC (2014) Resource competition assays between the African big-headed ant, Pheidole megacephala (Fabricius) and the invasive Argentine ant, Linepithema humile (Mayr): mechanisms of inter-specific displacement. Ecological Entomology 39, 501–510.10.1111/een.12126CrossRefGoogle Scholar
Nelson, RA, MacArthur-Waltz, DJ and Gordon, DM (2023) Critical thermal limits and temperature-dependent walking speed may mediate coexistence between the native winter ant (Prenolepis imparis) and the invasive Argentine ant (Linepithema humile). Journal of Thermal Biology 111, 103392.10.1016/j.jtherbio.2022.103392CrossRefGoogle ScholarPubMed
Ness, JH and Bronstein, IL (2004) The effects of invasive ants on prospective ant mutualists. Biological Invasions 6, 445–461.10.1023/B:BINV.0000041556.88920.ddCrossRefGoogle Scholar
O'Neill, BC, Kriegler, E, Ebi, KL, Kemp-Benedict, E, Riahi, K, Rothman, DS, van Ruijven, BJ, van Vuuren, DP, Birkmann, J, Kok, K, Levy, M and Solecki, W (2017) The roads ahead: narratives for shared socioeconomic pathways describing world futures in the 21st century. Global Environmental Change 42, 169–180.10.1016/j.gloenvcha.2015.01.004CrossRefGoogle Scholar
Pejchar, L and Mooney, HA (2009) Invasive species, ecosystem services and human well-being. Trends in Ecology & Evolution 24, 497–504.10.1016/j.tree.2009.03.016CrossRefGoogle ScholarPubMed
Peterson, AT (2003) Predicting the geography of species’ invasions via ecological niche modeling. Quarterly Review of Biology 78, 419–433.10.1086/378926CrossRefGoogle ScholarPubMed
Pratt, CF, Constantine, KL and Murphy, ST (2017) Economic impacts of invasive alien species on African smallholder livelihoods. Global Food Security-Agriculture Policy Economics and Environment 14, 31–37.10.1016/j.gfs.2017.01.011CrossRefGoogle Scholar
Pysek, P, Hulme, PE, Simberloff, D, Bacher, S, Blackburn, TM, Carlton, JT, Dawson, W, Essl, F, Foxcroft, LC, Genovesi, P, Jeschke, JM, Kuehn, I, Liebhold, AM, Mandrak, NE, Meyerson, LA, Pauchard, A, Pergl, J, Roy, HE, Seebens, H, van Kleunen, M, Vila, M, Wingfield, MJ and Richardson, DM (2020) Scientists’ warning on invasive alien species. Biological Reviews 95, 1511–1534.10.1111/brv.12627CrossRefGoogle ScholarPubMed
Roura-Pascual, N, Bas, JM, Thuiller, W, Hui, C, Krug, RM and Brotons, L (2009) From introduction to equilibrium: reconstructing the invasive pathways of the Argentine ant in a Mediterranean region. Global Change Biology 15, 2101–2115.10.1111/j.1365-2486.2009.01907.xCrossRefGoogle Scholar
Sanders, NJ and Suarez, AV (2011) Elton's insights into the ecology of ant invasions: lessons learned and lessons still to be learned. In Richardson DM (ed.), Fifty Years of Invasion Ecology: The Legacy of Charles Elton, 1st Edn. Chichester, West Sussex, UK: Blackwell Publishing Ltd, pp. 239–251.Google Scholar
Sanmartin-Villar, I, Csata, E and Jeanson, R (2021) Variability in activity differs between castes in the ant Linepithema humile. Ecological Entomology 46, 1373–1378.10.1111/een.13075CrossRefGoogle Scholar
Sarnat, EM (2008) PIAkey: Identification guide to ants of the Pacific Islands, Edition 2.0, Lucid v. 3.4. USDA/APHIS/PPQ Center for Plant Health Science and Technology and University of California — Davis. Available at http://idtools.org/id/ants/pia/Google Scholar
Schilman, PE, Lighton, JRB and Holway, DA (2007) Water balance in the Argentine ant (Linepithema humile) compared with five common native ant species from southern California. Physiological Entomology 32, 1–7.10.1111/j.1365-3032.2006.00533.xCrossRefGoogle Scholar
Shi, J, Luo, Y-Q, Zhou, F and He, P (2010) The relationship between invasive alien species and main climatic zones. Biodiversity and Conservation 19, 2485–2500.10.1007/s10531-010-9855-4CrossRefGoogle Scholar
Si-qi, CHEN, Yi, ZHaO, Yong-yue, LU, Hao, RaN and Yi-juan, XU (2022). First record of the little fire ant, Wasmannia auropunctata (Hymenoptera: Formicidae), in Chinese mainland. Journal of Integrative Agriculture 21, 1825–1829.10.1016/S2095-3119(22)63903-0CrossRefGoogle Scholar
Silverman, J and Buczkowski, G (2016) 13 Behaviours mediating ant invasions. In Sweis J and Sol D (eds), Biological Invasions and Animal Behaviour. Cambridge, UK: Cambridge University Press, pp. 221–224.10.1017/CBO9781139939492.014CrossRefGoogle Scholar
Sopniewski, J, Scheele, BC and Cardillo, M (2022) Predicting the distribution of Australian frogs and their overlap with Batrachochytrium dendrobatidis under climate change. Diversity and Distributions 28, 1255–1268.10.1111/ddi.13533CrossRefGoogle Scholar
Souza, E, Follett, PA, Price, DK and Stacy, EA (2008) Field suppression of the invasive ant Wasmannia auropunctata (Hymenoptera: Formicidae) in a tropical fruit orchard in Hawaii. Journal of Economic Entomology 101, 1068–1074.10.1603/0022-0493(2008)101[1068:FSOTIA]2.0.CO;2CrossRefGoogle Scholar
Suhr, EL, O'Dowd, DJ, Suarez, A, Cassey, P, Wittmann, TA, Ross, J and Cope, RC (2019) Ant interceptions reveal roles of transport and commodity in identifying biosecurity risk pathways into Australia. Neobiota 53, 1–24.10.3897/neobiota.53.39463CrossRefGoogle Scholar
Suiter, DR, Gochnour, BM, Holloway, JB and Vail, KM (2021) Alternative methods of ant (Hymenoptera: Formicidae) control with emphasis on the Argentine ant, Linepithema humile. Insects 12, 487.10.3390/insects12060487CrossRefGoogle ScholarPubMed
Teles, WS, Silva, DdeP, Vilela, B, Lima-Junior, DP, Pires-Oliveira, JC and Miranda, MS (2022). How will the distributions of native and invasive species be affected by climate change? Insights from Giant South American Land Snails. Diversity-Basel 14, 467.Google Scholar
Verlinden, M, De Boeck, HJ and Nijs, I (2014) Climate warming alters competition between two highly invasive alien plant species and dominant native competitors. Weed Research 54, 234–244.10.1111/wre.12076CrossRefGoogle Scholar
Vogel, V, Pedersen, JS, Giraud, T, Krieger, MJB and Keller, L (2010) The worldwide expansion of the Argentine ant. Diversity and Distributions 16, 170–186.10.1111/j.1472-4642.2009.00630.xCrossRefGoogle Scholar
Vonshak, M, Dayan, T, Ionescu-Hirsh, A, Freidberg, A and Hefetz, A (2010) The little fire ant Wasmannia auropunctata: a new invasive species in the Middle East and its impact on the local arthropod fauna. Biological Invasions 12, 1825–1837.10.1007/s10530-009-9593-2CrossRefGoogle Scholar
Walters, AC and Mackay, DA (2005) Importance of large colony size for successful invasion by Argentine ants (Hymenoptera: Formicidae): evidence for biotic resistance by native ants. Austral Ecology 30, 395–406.10.1111/j.1442-9993.2005.01481.xCrossRefGoogle Scholar
Warren, DL and Seifert, SN (2011) Ecological niche modeling in Maxent: the importance of model complexity and the performance of model selection criteria. Ecological Applications 21, 335–342.10.1890/10-1171.1CrossRefGoogle ScholarPubMed
Wetterer, JK and Porter, SD (2003) The little fire ant, Wasmannia auropunctata: distribution, impact, and control. Sociobiology 42, 1–41.Google Scholar
Wild, AL (2004) Taxonomy and distribution of the Argentine ant, Linepithema humile (Hymenoptera: Formicidae). Annals of the Entomological Society of America 97, 1204–1215.10.1603/0013-8746(2004)097[1204:TADOTA]2.0.CO;2CrossRefGoogle Scholar
Wu, T, Lu, Y, Fang, Y, Xin, X, Li, L, Li, W, Jie, W, Zhang, J, Liu, Y, Zhang, L, Zhang, F, Zhang, Y, Wu, F, Li, J, Chu, M, Wang, Z, Shi, X, Liu, X, Wei, M, Huang, A, Zhang, Y and Liu, X (2019) The Beijing climate center climate system model (BCC-CSM): the main progress from CMIP5 to CMIP6. Geoscientific Model Development 12, 1573–1600.10.5194/gmd-12-1573-2019CrossRefGoogle Scholar
Zhang, Y, Hughes, AC, Zhao, Z, Li, Z and Qin, Y (2022) Including climate change to predict the global suitable area of an invasive pest: Bactrocera correcta (Diptera: Tephritidae). Global Ecology and Conservation 34, e02021.10.1016/j.gecco.2022.e02021CrossRefGoogle Scholar
Zhang, Z, Chen, L, Zhang, X and Li, Q (2023) Prediction of the potential distributions of Prunus salicina Lindl., Monilinia fructicola, and their overlap in China using MaxEnt. Journal of Fungi 9, 189.10.3390/jof9020189CrossRefGoogle Scholar
Zhao, R, Chu, X, He, Q, Tang, Y, Song, M and Zhu, Z (2020) Modeling current and future potential geographical distribution of Carpinus tientaiensis, a critically endangered species from China. Forests 11, 774.10.3390/f11070774CrossRefGoogle Scholar
Zhao, H, Xian, X, Guo, J, Yang, N, Zhang, A, Chen, B, Huang, H and Liu, W (2022) Monitoring the little fire ant, Wasmannia auropunctata (Roger 1863), in the early stage of its invasion in China: predicting its geographical distribution pattern under climate change. Journal of Integrative Agriculture 22, 2783–2795.10.1016/j.jia.2022.12.004CrossRefGoogle Scholar
Zhu, G-L, Tang, Y-Y, Limpanont, Y, Wu, Z-D, Li, J and Lv, Z-Y (2019) Zoonotic parasites carried by invasive alien species in China. Infectious Diseases of Poverty 8, 2.10.1186/s40249-018-0512-6CrossRefGoogle ScholarPubMed
Figure 0

Figure 1. The distribution data of L. humile and W. auropunctata.

Figure 1

Figure 2. Contribution rate of the five selected environmental variables (A, B) and model evaluation (C, D). Panel A shows the contribution rate of the environmental variables for L. humile, while panel B shows the contribution rate for W. auropunctata. Panel C and D show the model evaluation for L. humile and W. auropunctata in terms of AUC.

Figure 2

Figure 3. Potential geographic distribution of L. humile and W. auropunctata under current climate conditions. Panel A shows the suitable area for L. humile, panel B shows the suitable area for W. auropunctata.

Figure 3

Table 1. The top 10 countries with the largest suitable areas for Linepithema humile and Wasmannia auropunctata

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Figure 4. Potential geographical distribution of L. humile under four future climate scenarios. A-D showed the potential geographical distribution of L. humile in 2050 under the scenarios SSP126, SSP245, SSP370, and SSP585, respectively.

Figure 5

Figure 5. Potential geographical distribution of W. auropunctata under four future climate scenarios: SSP126, SSP245, SSP370, and SSP585 (A–D).

Figure 6

Figure 6. The overlap areas of potential geographic distributions of L. humile and W. auropunctata under current (A) and future SSP585 climate scenario (B).

Figure 7

Table 2. Top ten countries with the largest expansion of suitable overlap areas of L. humile and W. auropunctata under the SSP585 climate change scenario, including percentage increase