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Environmental filtering and spatial processes equally contributed to macroinvertebrate metacommunity dynamics in the highly urbanized river networks in Shenzhen, South China



Disentangling the relative roles of environmental filtering and spatial processes in structuring ecological communities is a central topic in metacommunity ecology. Metacommunity ecology in the temperate river ecosystems has been well developed, while less attention has been paid to subtropical urban river networks. Here, we examined the ecological factors and seasonal difference in structuring macroinvertebrates metacommunity assembly in the subtropical urban river networks in Shenzhen, South China.


Our results revealed that there was no significant distinction of macroinvertebrate community composition among seasons, with only the relative abundance of Mollusca and Odonata significantly differed in both wet and dry seasons. One possible explanation was that most macroinvertebrates are generally pollution-tolerant taxa characterized with nonseasonal life cycle. In addition, distance-based redundancy analysis and variation partitioning approach revealed that metacommunity was determined equally by the environmental and dispersal-related factors. Further, our results showed that, although a slight temporal variation of relative contribution, the identity and explanation power of ecological factors were different among seasons. Specifically, stronger environmental filtering structuring community dynamics was observed in the dry than wet seasons, which might be owing to higher environmental heterogeneity under a low water-flow condition. Moreover, we detected that the influence of spatial processes was stronger in the wet than dry seasons, indicating an obvious dispersal processes due to high connectivity among sites.


Overall, our results revealed that environmental and spatial factors equally explained variations of macroinvertebrate metacommunity, implying the necessity of considering dispersal-related processes structuring ecological communities in river bioassessment programs. Moreover, degraded habitat conditions and water quality were the predominant factors that affected macroinvertebrate communities, indicating the significance and feasibility of improving local abiotic conditions to sustain local biodiversity. Further, our findings revealed the importance of seasonal dynamics of these urban river networks in structuring macroinvertebrate metacommunity. Thereby, our study improves the understanding of ecological processes governing macroinvertebrate metacommunity and underlines the idea that community ecology studies should go beyond the single snapshot survey in river networks.


Disentangling the underlying processes driving spatial-temporal variations of ecological communities is a major topic in modern community ecology (Chase et al. 2020; Chase and Myers 2011; Cottenie 2005). Two primary processes have been proposed to explain the mechanisms governing ecological communities (Chase 2003; Tonkin et al. 2016). The niche-based deterministic processes (e.g., environmental filtering and biological interactions within and among species) assumes that species coexistence is premised on the differentiation of ecological niches (Keddy 1992). In this case, species sharing similar functional traits should occupy similar environments (Carvalho et al. 2019). Besides, stochastic processes assumes that there is no ecological differentiation between species, and it is believed that spatial factors (e.g., related to species dispersal) are important in structuring community assembly (Chave 2004; Hubbell and Borda-De-Agua 2004). Recently, metacommunity theory provides a comprehensive framework that integrating both environmental filtering and dispersal-related processes explaining divergence among community composition across scales of space and time (Chase et al. 2020; Leibold et al. 2004). Theoretical and empirical research suggest that both basic processes should be jointly responsible for the variations in community composition, but the relative roles of these processes may depend largely on ecosystem types (Logue et al. 2011), seasonal dynamics (Chen et al. 2019; Csercsa et al. 2018; Li et al. 2020), and focal biological groups (He et al. 2020; Schmera et al. 2016; Wang et al. 2020).

Urban rivers possess many attributes that make them ideal natural systems for studying the relative contribution of environmental filtering and dispersal processes for aquatic organisms (Shu et al. 2020). As a highly disturbed ecosystem, urban rivers exhibited strong environmental gradients due to a series of anthropogenic stressors, such as nutrient enrichment, elevated temperature, and altered instream substrate composition (Allan 2004; Luo et al. 2018; Wang et al. 2018). These strong environmental gradients can serve as environmental filters to regulate community structure and diversity (Castro et al. 2018), which increased the strength of deterministic processes governing aquatic metacommunity. Besides, river hydrological alterations (e.g., altered macrosystem dynamics and damming) would limit the processes of organism dispersal via damming and humanities building (Raabe and Hightower 2014; Wan et al. 2018). These disturbances could cause rapid and difficult-to-reverse ecological changes that impede the delivery of ecosystem services (Isabwe et al. 2018). However, the mechanisms underlying ecological communities in highly urbanized city river networks remain unclear (Bourassa et al. 2017; Gál et al. 2019).

Recent studies have frequently emphasized that mechanisms governing community assembly in river systems varied among seasons (Chen et al. 2019; Fernandes et al. 2013; Li et al. 2020). Ecosystems are dynamic, especially for subtropical rivers, even on a relatively short time scale (Datry et al. 2016). In this case, seasonality is a crucial driver of environmental heterogeneity and connectivity among habitats (Fernandes et al. 2014; Vanschoenwinkel et al. 2010). For instance, in the wet season, high flow has increased locations connection and is beneficial for aquatic organisms expanding their ranges into adjacent locations (Sarremejane et al. 2017a). In this regard, spatial signal of community would be expected to enhance due to sufficient dispersal under high connectivity (Cottenie et al. 2003). Besides, snapshot surveys may misrepresent the relative contribution of specific processes of community assembly, because they assumed that the mechanism governing community variations is stable through time (Csercsa et al. 2018; Li et al. 2020). Thus, teasing apart the seasonal difference of these basic processes would provide more detailed information for understanding the mechanisms of community assembly.

To our knowledge, the community assembly mechanisms were well developed in temperate river ecosystems (Cilleros et al. 2017); however, for subtropical urban river networks, this knowledge is still poorly understood (Chen et al. 2019). Moreover, testing seasonal difference of these processes in subtropical river ecosystems are still lacking (Chen et al. 2019; Isabwe et al. 2018; Li et al. 2020). In this study, we selected macroinvertebrtae, a widely used ecological indicator in environmental monitoring and bioassessment programs (Rosenberg and Resh 1993), as the model organisms to understand the mechanisms of community assembly and the seasonal shifts of the involved mechanisms (Wang et al. 2020). Here, we tested the following three predictions. First, macroinvertebrate community assembly would be primarily determined by environmental filtering under harsh conditions, because intensive anthropogenic stressors can constitute a strict environmental filter to select particular organisms (Chase 2007). Second, we predicted a higher biodiversity and stronger environmental filtering structuring community assembly in the dry than wet season because higher habitat heterogeneity in the dry season would provide more niches for macroinvertebrtae (Sarremejane et al. 2017a). Third, we hypothesized that spatial processes governing community assembly was stronger in the wet than dry seasons due to a stronger dispersal effect induced by higher connectivity (Fernandes et al. 2013).


Study area and sampling sites

The present study was conducted in Shenzhen (113° 43′–114° 38′ E, 22° 24′–22° 52′ N), a coastal megacity located in the Southeast part of China. This city area comprises approximately 1997 km2 and with 13 million inhabitants in 2019 (Shenzhen Statistical Yearbook 2019). Shenzhen is characterized by a subtropical monsoon climate, with an average annual temperature of 24 °C and an average annual precipitation of 1882 mm. The precipitation of Shenzhen has a great seasonal fluctuations, with 96.3% of rain fall concentrated during the wet season (April to September) (Shenzhen Climate Bulletin 2019). Specifically, due to the fact that main watersheds in Shenzhen are typical rain-source urban rivers, river runoff and flow volumes are closely linked to precipitation (Liu et al. 2019).

Shenzhen has experienced enormous urbanization development and has grown to be one of the flourishing cities in the last four decades (Qian et al. 2020). Besides, due to rapidly developing economy, intensive anthropogenic activities and insufficient wastewater treatment plant, rivers in Shenzhen have suffered a series of environmental pollution problems, such as ecosystem health deterioration (Ng et al. 2011), water quality degradation (Liu et al. 2019), etc. However, macroinvertebrate community patterns and the mechanisms underlying community assembly in this region received far less attention.

In this study, a total of 62 sampling sites were sampled in August (wet season) and December (dry season) in 2019 (Fig. 1). These sites were roughly evenly distributed in Maozhouhe River (MZHR: 12 sites), Guanlanhe River (GLHR: 13 sites), Shenzhenhe River (SZHR: 13 sites), Pingshanhe River (PSHR: 12 sites), and Dapenghe River (DPHR: 12 sites).

Fig. 1

The study area and sampled watersheds in Shenzhen, South China

Macroinvertebrate sampling and identification

At each sampling site, we refer to a multi-habitat sampling technique in the field, with five replicates randomly sampled along a 100-m-long stretch reach (Barbour et al. 1999). The main habitats were selected, including different substrate (i.e., cobble, pebble, gravel, and sand and silt), riparian zone, and submerged macrophytes (Luo et al. 2018). For each replicate, benthic materials were collected using a D-frame kick (30 cm wide, 250 μm mesh size) in 30 × 30 cm per sample unit (0.09 m2) (Castro et al. 2020). Then, benthic materials were washed in the field using a 500-μm copper mesh sieve. The five subsamples with 0.45 m2 area for each sampling site were handpicked carefully from benthic materials on a porcelain plate and then were preserved with 75% alcohol. In the laboratory, macroinvertebrates were identified and counted under a stereomicroscope (Olympus; usually for aquatic insects) or a microscope (Imager A2; usually for Oligochaeta and certain Diptera insects). Specimens were identified to possible lowest taxonomic level (usually to genus), and Oligochaeta and Mollusca were identified to the species level using relevant taxonomic keys (Brinkhurst 1986; Epler 2001; Morse et al. 1994; Thorp and Covich 2001; Wiggins 1996; Zhou et al. 2003).

Local environmental variables

Prior to macroinvertebrate sampling, environmental variables were measured at each sampling site. Water depth (WD) and velocity (Vel) were averaged using a calibrated stick and a LJD-10 flowmeter following a zyg-zag pattern (right-mid-left) in each sampling site, respectively. River width (RW) and turbidity (Tur) were measured by a diastimeter and turbidity meter, respectively. The composition of the substrate by visually estimating the percentages of boulder (> 256 mm), cobble (64–256 mm), pebble (32–64 mm), gravel (2–32 mm), sand and silt (< 2 mm) at each sampling site using a 1 m2 grid (Kondolf 1997). Furthermore, we calculated substrate heterogeneity (Div_substrate) from the Simpson index considering the composition of the substrate (Firmiano et al. 2020). Water temperature (WT), pH, dissolved oxygen (DO), and conductivity (Cond) were acquired in the field with a YSI Professional Plus Water Quality Sonde. Besides, 1 L water sample was collected using an acrylic water sampler and preserved in 4 °C and then transported to laboratory within 12 h for further analysis. In laboratory, total nitrogen (TN), total phosphorus (TP), ammonium nitrogen (NH4+-N), chemical demand oxygen (CODCr), permanganate index (PI), and biochemical oxygen demand over 5 days (BOD5) were measured according to standard methods (EPBC 2002).

Spatial factors analysis

To model the spatial relations of community structure among sampling sites at multiple scales, the principal coordinates of neighbor matrices (PCNM) approach was used to provide spatial factors based on overland distances among sampling sites for further analysis (Li et al. 2019). This approach is widely used for modeling spatial structures in biological communities (Legendre and Legendre 2012). We only retained those associated with significant Moran's I and positive eigenvalues because they represent a potential positive autocorrelation between spatial points at different scales (Dray and Legendre 2008). The first larger spatial eigenvalues indicate broad-scale spatial relations between locations and last spatial vectors show smaller scale variation among sites (Borcard et al. 2004; Borcard and Legendre 2002). Eventually, we obtained 25 spatial factors with positive eigenvalues for constrained ordination models. The spatial factors were obtained using the function pcnm in the R package vegan (Legendre et al. 2013).

Data analysis

Prior to statistical analysis, local environmental variables (except for pH), and biodiversity indices were transformed by log (x + 1) or square root (i.e., proportional data: substrate composition data and the relative abundance of dominant groups) to improve normality. We used Mann-Whitney U tests to detect difference of local environmental variables, the relative abundance of dominant groups, and biodiversity indices across wet and dry seasons. Then, the environmental heterogeneity for each sampling period was examined using the permutational analysis of multivariate dispersions (PERMDISP) (Legendre and Legendre 2012) based on Euclidean distance considering all the standardized environmental variables. Higher average distance indicates the higher environmental heterogeneity (Anderson 2006). Besides, we ran nonmetric multidimensional scaling (NMDS) using the Bray-Curtis similarity distance based on abundance data to distinguish differences in community structures among seasons (Legendre and Legendre 2012). SIMPER analysis was used to identify species that contributed most to community dissimilarity among seasons (Clarke 1993). Besides, one-way analysis of similarities (ANOSIM) with 999 permutations was employed to examine whether taxonomic composition of macroinvertebrate significantly differed among five watersheds (Clarke 1993).

To elucidate the relative roles of local environmental variables and spatial factors structuring macroinvertebrate community, we employed distance-based redundancy analysis (db-RDA) (Legendre and Anderson 1999) and associated variation partitioning procedures (Legendre and Legendre 2012). Distance-based redundancy analysis (db-RDA) was used to examine the relationships between macroinvertebrate community structure and local environmental variables and spatial factors, respectively. Prior to db-RDA analysis, all environmental variables were scaled to zero mean and unit variance to allow comparisons. Then, we removed highly correlated environmental variables (Spearman r > 0.75) to reduce multicollinearity in the R package Hmisc (Harrell 2016). Both environmental and spatial factors were screened by a forward selection procedure in the R package adespatial to identify a set of significant factors, respectively (Dray et al. 2017). Then we conducted variation partitioning analysis (Legendre and Legendre 2012) to obtain the pure environmental variables, pure spatial factors, their shared fractions, and unexplained fractions with the varpart function in the R package Vegan (Oksanen et al. 2017). Additionally, we examined the above fractions by means of the Monte Carlo test with 999 permutations at a significance level of α = 0.05 (Oksanen et al. 2017).

Mann-Whitney U tests analysis was conducted on SPSS version 25.0. The biodiversity index calculation, NMDS analysis, SIMPER analysis, and one-way analysis of similarities (one-way ANOSIM) analysis were conducted using the software PRIMER 6.0 and PERMANOVA+. Other statistical analysis were performed on R version 3.6.2 (R Developement Core Team 2018).


Environmental condition

In general, except for water temperature (WT), pH, turbidity, river width (RW), ammonium nitrogen (NH4+-N), and total phosphorus (TP), half of the 20 environmental variables were not significantly differed between wet and dry seasons (Table 1). Among them, certain environmental variables related to habitat conditions, such as substrate composition, substrate heterogeneity index, and water depth (WD) were not differed among wet and dry seasons. Specially, wet season had higher water temperature (WT), turbidity, river width (RW), chemical demand oxygen (CODCr), permanganate index (PI), biochemical oxygen demand over 5 days (BOD5), ammonium nitrogen (NH4+-N), while higher values of dissolved oxygen (DO), pH, total nitrogen (TN), conductivity, and velocity were detected in the dry season. PERMDISP analysis revealed that there was no significant difference in the variance of the environmental heterogeneity among seasons (F = 0.627; P > 0.05). However, in terms for the variation of the environmental heterogeneity, the dry season (average Euclidean distance: 6.92) was more variable than the wet season (average Euclidean distance: 6.57).

Table 1 Environmental variables across the 62 sampling sites in the wet and dry seasons. **P < 0.01 or *P < 0.05 indicate the significant difference among seasons based on Mann-Whitney U tests

Macroinvertebrate community composition

A total of 21,714 individuals comprising 158 taxa were collected, belonging to 4 phyla, 8 classes, 20 orders, 74 families, and 141 genera in the entire sampling period. Aquatic insects accounted for 75.32% (119 taxa), followed by Oligochaeta (19 taxa, 12.03%), Mollusca (19 taxa, 12.03%), and Nematoda (1 taxon, 0.63%). Species with higher occurrence frequency were Limnodrilus sp., Limnodrilus hoffmeisteri, Polypedilum sp., Physa acuta, and Biomphalaria straminea.

In general, 112 and 132 taxa were sampled in the wet and dry seasons, respectively. The top three dominant species in the dry season were Limnodrilus sp. (relative abundance: 8.63%), Limnodrilus hoffmeisteri (6.98%), and Limnodrilus claparedeianus (6.21%), while Chironomus sp. (5.69%), Polypedilum sp. (5.69%), and Limnodrilus sp. (5.45%) were dominated in the wet season. NMDS analysis showed that there was no significant distinction of macroinvertebrate community composition among seasons (Fig. 2). Only the relative abundance of Mollusca and Odonata were significantly differed among seasons (Supplement Table 1). SIMPER analysis showed that Limnodrilus sp. and Limnodrilus hoffmeisteri were among the most present taxa in both seasons. Other characteristic taxa were Limnodrilus claparedeianus, Branchiura sowerbyi, and Chironomus kiiensis for the wet season, while Biomphalaria straminea, Chironomus sp., and Polypedilum sp. for the dry season (Table 2).

Fig. 2

Non-metric multidimensional scaling (NMDS) of macroinvertebrate community among wet and dry seasons in Shenzhen, South China

Table 2 Results of top 5 ranked SIMPER species in both wet and dry seasons

Spatially, differences in macroinvertebrate composition were evident among the five watersheds (Supplement Figure 1). One-way ANOSIM analysis indicated that all pairwise comparisons of community differed significantly among five watersheds (Global R: 0.117–0.608, P < 0.05), except for GLHR and SZHR (Global R = 0.005, P > 0.05), PSHR and DPHR (Global R = 0.042, P > 0.05), MZHR and GLHR (Global R = 0.044, P > 0.05). More specifically, in PSHR and DPHR, aquatic insects (Exclusion of Chironomidae) accounted for 50.81%, 53.14% of the total abundance in the wet and dry seasons, respectively. In MZHR, GLHR, and SZHR, Oligochaeta and Chironomidae constituted 0–100% of the total abundance with an average value of 71.48% and 71.36% in the wet and dry seasons, respectively.

Richness, Simpson index and Shannon-Wiener index differed significantly among seasons, with higher values in the dry season (Fig. 3). In contrast, Evenness did not significantly differ among seasons.

Fig. 3

Richness, Simpson index, Shannon-Wiener index, and Evenness of macroinvertebrate community among wet and dry seasons, respectively. **P < 0.01 indicates the significant difference among seasons based on Mann-Whitney U tests

Key environmental and spatial factors affecting community structure

Forward selection procedure showed that water temperature (WT), water depth (WD), pH, %sand and silt, and total nitrogen (TN) were significantly associated with the macroinvertebrate communities in the wet season, while water depth (WD), chemical demand oxygen (CODCr), dissolved oxygen (DO), total phosphorus (TP), and permanganate index (PI) proved to be important in shaping macroinvertebrate communities in the dry season (Table 3; Fig. 4). 

Spatial factors analysis based on forward selection procedure showed that PCNM1, PCNM2, PCNM4, and PCNM5 were retained in the wet season, whereas PCNM1, PCNM5, PCNM2, PCNM8, PCNM4, and PCNM28 were retained in the dry season (Table 3; Fig. 4).

Table 3 Results of forward selection procedure in the db-RDA analysis in both wet and dry seasons
Fig. 4

Distance-based constrained ordination (db-RDA) of macroinvertebrate community for a environmental variables and b spatial factors in the wet season, and for c environmental variables and d spatial factors in the dry season. The significant environmental and spatial variables were selected based on forward selections (P < 0.05)

Relative roles of environmental and spatial factors

Variation partitioning procedure revealed that the pure environmental variables, spatial factors, and their shared effects jointly explained 49% and 42% of the community variation in the wet and dry seasons (Fig. 5), respectively. The relative roles of environmental and spatial factors varied slightly among seasons. Specifically, spatial factors explained more of the variations (10%; Monte Carlo permutations test: P < 0.01) compared to environmental variables (8%; P < 0.05) in the wet season. Conversely, environmental variables accounted for 9% (P < 0.01) of the community variations than spatial factors (8%; P < 0.01) in the dry season. However, the shared fractions (i.e., explained jointly by both environmental variables and spatial factors) accounted for most of the variations, with 31% (P < 0.01) and 25% (P < 0.01) of the community variations explained in both wet and dry seasons, respectively.

Fig. 5

Variation partitioning of macroinvertebrate metacommunity into pure environmental variables (Env), pure spatial factors (Spa), their shared fractions (Shared), and the unexplained variations among wet and dry seasons. Values represent the adjusted R2 values. **P < 0.01 or *P < 0.05 represent significant results based on the Monte Carlo permutations test


Our results provide the first detailed description of macroinvertebrate community composition and seasonal dynamics in the Shenzhen river networks. There were no obvious differences of macroinvertebrate community structure among seasons, which might be owing to relative abundance of tolerant taxa with nonseasonal life history. Further, a novel finding revealed that both environmental filtering and spatial processes equally contributed to the assembly of macroinvertebrate metacommunity. Importantly, our results showed that the identity and explanatory power of environmental and spatial factors differed during the wet and dry seasons.

Mechanisms underlying macroinvertebrate community assembly

Contradicted to the first prediction, our results detected that macroinvertebrate metacommunity was determined equally by environmental filtering and spatial processes. These findings, however, do not fit well with previous studies that deterministic processes dominated in macroinvertebrate metacommunity assembly in other river ecosystems (He et al. 2020; Li et al. 2020). One possible explanation was that macroinvertebrate communities in this basin are likely to comprise considerable abundance of general tolerant taxa (e.g., Oligochaeta and Chironomidae larva), whose persistence is less sensitive to local environmental conditions (Kim et al. 2008; Rosenberg and Resh 1993). Another explanation was that regional habitat homogenization in urban ecosystems would potentially weaken the correspondence of ecological communities to local environments conditions (Bourassa et al. 2017). Besides, one that cannot be ignored was that spatially structured environmental variables contributed more variations for this metacommunity. However, the shared effects of environmental and spatial factors are difficult to interpret. Generally, such shared effects are typical in studies of aquatic metacommunities (Heino et al. 2015; Vilmi et al. 2016). Although we did not identify a dominance of environmental filtering shaping macroinvertebrtae metacommunity, our results revealed that certain local environmental variables related to nutrients (e.g., TN, PI, CODCr) and physical habitat conditions (e.g., WT and substrate composition) were important for macroinvertebrate communities. These variables were evidenced as the critical factors affecting the relative abundance and occurrence frequency of macroinvertebrate communities (Li et al. 2020; Wang et al. 2020).

Our results revealed that spatial factors also played important roles in explaining variations in macroinvertebrate metacommunity, implying the necessity to consider the dispersal-related processes in routine monitoring and assessment programs. We infer that dispersal limitation generated strong spatial signals in macroinvertebrtae metacommunity. Possible elements contributing to the results include the organism dispersal ability and dispersal constrains (e.g., low-head dam and buildings) (Crook et al. 2015; Csercsa et al. 2018). Spatial factors with large eigenvalues (e.g., PCNM1 and PCNM2) were selected based on a forward selection procedure, indicating that broader scale spatial processes were important in driving the macroinvertebrate metacommunity (Borcard and Legendre 2002). Besides, the dominant species (e.g., Limnodrilus hoffmeisteri and Biomphalaria straminea) in our study were small-bodied aquatic passive groups with limited dispersal ability. Meanwhile, we should realize that these effects would be expected to enhance under the pressure of dispersal constrains. For instance, some low-head dames located in channels would hinder the route of aquatic passive organisms (Wan et al. 2018), while intensive buildings and cultural facilities along the channels would cause negative effects on terrestrial passive and active groups (Urban et al. 2006).

Although the relative importance of environmental and spatial factors varied slightly among seasons, we indeed observed that the identity and explanatory rate of both factors differed between wet and dry seasons. Thus, our results clearly support the prediction that there exist the seasonal shifts of community assembly mechanisms in the study region, and further stress the significance of exploring community assembly mechanisms from the temporal perspective (Li et al. 2020). In terms of the slightly seasonal variation of community assembly, it might be related to a fact that nonsignificant changes in assemblage composition displayed along homogeneous environmental conditions (PERMDISP analysis). One possible explanation was that most macroinvertebrates in urban river ecosystems are generally pollution-tolerant taxa characterized with nonseasonal life cycle (Carlisle and Hawkins 2008). Similarly, a previous relevant study has showed that the seasonal changes in macroinvertebrate communities in the urban river ecosystems were lower than the least-disturbed rivers (Wang et al. 2018).

In line with the second prediction, we found higher biodiversity embodied in the dry than wet seasons. This could be related to higher heterogeneity in microhabitats of macroinvertebrate communities during the period of low water-flow currents and connectivity (Aiello-Lammens et al. 2017; Chen et al. 2019). Our results also detected that stronger environmental filtering structuring community assembly in the dry than wet seasons, implying that deterministic processes dominated in driving community dynamics during the low water-flow conditions (Sarremejane et al. 2017b). This result was reasonable because the strength of environmental filtering is expected to be stronger with increasing environmental harshness during the low water-flow currents period (Boulton 2003; Sarremejane et al. 2017a). In our case, several environmental variables (e.g., PI, DO, CODCr, and TP) significantly explained the variations in macroinvertebrate communities, thus serve as environmental filters that select for the most resistant/adapted taxa in the regional species pool. Additionally, we found a higher predictive power of spatial factors over metacommunity structures in the wet than dry seasons. A fast recolonization after a flood event may potentially influence the relative contribution of dispersal-related processes on biological communities (Datry et al. 2016). Besides, connectivity among locations would be intensified when flushing water regimes occurred and can act as an excellent proxy for aquatic organism dispersal (Chaparro et al. 2018). Further, one point we cannot ignore is that spatial signal could be enhanced under the massive fly of fledged adult insects in such seasons. However, we only focused on the larvae of macroinvertebrate in the present study, which may ignore the dispersal patterns of fledged adult insects and then limit the representativeness of our results. Thus, different dispersal mode studies of aquatic larvae and adults must be considered in future studies.

It should be noted that the variation partitioning approach employed in our study did not explain all the variations in macroinvertebrate metacommunity, indicating that other community assembly mechanisms might be working in the meantime. These other potential important mechanisms may include species interactions, unmeasured environmental variables and historical process (Chase 2003; Heino et al. 2015; Vellend et al. 2014). Although difficult to quantify the potential influences, these factors should also be responsible for variations in metacommunity structure. To better explore the key mechanisms underlying macroinvertebrate metacommunity in subtropical river networks, more effective statistical methodology and experimental consideration through spatial-temporal scale need to be considered.

Implications for the watershed management and biodiversity monitoring

Urban rivers support significant biodiversity and provide essential ecosystem services (Volker and Kistemann 2011). However, urban rivers have suffered substantial decline of aquatic biodiversity resulting from various anthropogenic stressors (Luo et al. 2018; Wang et al. 2018), but received relatively less attention (Higgins et al. 2019). Thus, unraveling the key driving force underlying community assembly is fundamental to accurate bioassessment, river management and restoration (Heino et al. 2015). Our results suggested that local environmental variables could mediate the macroinvertebrate community by increased nutrients and degraded habitat quality. Consequently, watershed management strategies should focus on improving local abiotic conditions to sustain local biodiversity (Luo et al. 2018; Wang et al. 2018). Furthermore, understanding the community assembly mechanisms should discriminate the signal of environmental filtering from the spatial effects (Heino et al. 2015; Li et al. 2020). If spatial processes are not considered, the mechanisms underlying community assembly may overestimate the importance of environmental factors (Dale et al. 2002). Our findings revealed that spatial factors and environmental variables play similar roles in influencing macroinvertebrate community. Thus, these findings highlight that watershed management and monitoring should emphasize simultaneously local environmental conditions and dispersal processes to better predict the responses of macroinvertebrate to human stressors. Specifically, given that the mechanisms governing macroinvertebrate community assembly vary among seasons, researchers should also emphasize the idea of long-term investigation at different seasons being necessary to enhance our understanding of their ecological dynamics.


In summary, our results demonstrated that both environmental and spatial factors equally dedicated to macroinvertebrate metacommunity assembly, implying that the necessity of considering the dispersal-related processes structuring ecological communities in river bioassessment and watershed management. Besides, degraded habitat conditions and water quality (e.g., TN, TP, pH, CODCr, and PI) were the predominant factors that affected macroinvertebrate communities, indicating the significance and feasibility of improving local abiotic conditions to sustain local biodiversity. Further, our findings revealed that the identity, explanatory power, and relative importance of assembly mechanisms varied among seasons. We thereby argue that one-season snapshot survey is inadequate for quantifying these ecological processes that influence metacommunity dynamics.

Availability of data and materials

All data will be available in the data center of Institute of Hydrobiology, Chinese Academy of Sciences ( after publication.



Distance-based redundancy analysis

one-way ANOSIM:

One-way analysis of similarities (ANOSIM)


Non-metric multidimensional scaling analysis


Permutational analysis of multivariate dispersions


Principal coordinates of neighbor matrices


Similarity percentage analysis


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We are grateful to Mr. Lei Liang, Miss. Fanghua Wang, and Dr. Xiao Qu who assisted in field sampling work. We also greatly appreciate the anonymous reviewers and the editors for giving valuable advice for this manuscript.


This work was supported by the program “Shenzhen City under the grant of Aquatic Ecological Monitoring and Assessment for Major rivers” (No. 2019-07-233) and Special Foundation for National Science and Technology Basic Research Program of China (grant No. 2019FY101903).

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ZL, ZX, and YC elaborated this research design. ZL conducted the investigation, data analyses, and writing. TZ and ZL conducted the species identification and data processing. ZX, YC, YC, and WW revised the manuscript and provided valuable suggestions. All authors participated in this research.

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Correspondence to Yushun Chen or Zhicai Xie.

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Supplementary Information

Additional file 1: Supplement Table 1

. Mean values ± SD of the relative abundance of macroinvertebrate groups in both wet and dry seasons, respectively. * (P < 0.05) indicate the significant difference among seasons based on Mann-Whitney U tests. Supplement Figure 1. Canonical Analysis of Principal Coordinates (CAP) ordination plots of five watershed macroinvertebrate abundance data (Bray-Curtis coefficient). Supplement Table 2. Summary of the results of Canonical Analysis of Principal Coordinates (CAP) for average differences in taxonomic composition of macroinvertebrate communities among five watersheds. Trace = sum of the canonical eigenvalues, Delta = the 1st eigenvalue. P-Values (in parentheses) were based on 999 permutations.

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Liu, Z., Zhou, T., Cui, Y. et al. Environmental filtering and spatial processes equally contributed to macroinvertebrate metacommunity dynamics in the highly urbanized river networks in Shenzhen, South China. Ecol Process 10, 23 (2021).

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  • Community assembly
  • Seasonal variation
  • Macroinvertebrate metacommunity
  • Environmental filtering
  • Spatial processes
  • Urban river