Anna Corli
Julia Walter2†
Christine S. Sheppard- 1Department of Earth and Environmental Sciences, University of Pavia, Pavia, Italy
- 2Landwirtschaftliches Technologiezentrum Augustenberg, Pflanzenproduktion, Rheinstetten, Germany
- 3Institute of Landscape and Plant Ecology, University of Hohenheim, Stuttgart, Germany
Climate change is altering precipitation patterns, with higher frequency and magnitude of extreme events. Specifically, longer and more pronounced waterlogged conditions are predicted after rain spells as well as more frequent droughts, especially in Central Europe. Such hydrological changes can severely affect species performance and alter the function of ecosystems, as well as favor plant invasions. Competition with native communities may change depending on water stress. Bunias orientalis is an invasive plant that may benefit from disturbance or precipitation changes. We conducted a 3-year mesocosm experiment in a common garden to investigate how invasion success of B. orientalis in native German grassland communities is affected by varying hydrological conditions (from very dry to waterlogged). We measured the establishment and growth of B. orientalis in varying water table depths in bare soil (simulating disturbance) vs. in the community. Establishment and biomass of B. orientalis was generally highest under non-stress conditions. The species was also highly tolerant to dry conditions, but only when growing in bare soil. However, performance of B. orientalis was generally low, whereby interspecific competition in communities greatly limited invasion success. This might be due to the low competitive ability of the species in conditions of hydrological stress and the near-natural grassland communities with an extensive mowing regime used in our experiment. Our results suggest that invasion success of B. orientalis in grasslands will not increase if precipitation patterns change toward more extreme events. However, disturbance that creates bare soil patches might favor B. orientalis under drought conditions.
Introduction
Climatic change leads to changes in precipitation patterns as well as higher frequency and magnitude of extreme events, which are projected to increase further during the 21st century for many areas (IPCC, 2014). Dry regions in mid latitudes and subtropics are expected to receive less annual precipitation whereas moist mid-latitudinal regions and higher latitudes receive more. However, many uncertainties regarding possible changes and impacts of annual precipitation in the future remain (Orlowsky and Seneviratne, 2013).
In regions that overall receive more precipitation such as Central Europe (IPCC, 2014), hydrological change is predicted to severely affect soil moisture, causing longer and more pronounced waterlogged conditions after extreme rain spells and flooding. Nevertheless, as already observed in Europe in the last decade (Hanel et al., 2018), changes in precipitation patterns might also result more frequently in dry conditions, causing hot and dry summers. Notably, Southern Germany has been demonstrated to be a geographical center in terms of deficit volumes of precipitation and duration of drought (Laaha et al., 2017). Such changes in water availability affect plant growth, and can change patterns of competition and facilitation between plants (Walter, 2018).
Grasslands are important biomes rich in biodiversity, accounting for nearly 25% of land surface on Earth (Gang et al., 2015); they offer key ecosystem services balancing the concentrations of global atmospheric greenhouse gases (O’Mara, 2012), protecting soil and water resources (Vogt et al., 2019) and providing livestock forage and therefore meat and milk for human consumption (O’Mara, 2012). Nevertheless, they are one of the most sensitive ecosystems to global climate change drivers (Seastedt and Pyšek, 2011), where anthropogenic influence accelerated their decline over the last decades (Czarniecka-Wiera et al., 2019). Indeed, as a consequence of abandonment and changing of traditional management toward intensification, European grasslands have experienced a decrease in species richness and changes in competitive regimes (Römermann et al., 2009), being also increasingly disturbed by frequent mowing or grazing (Stampfli et al., 2018).
Climate change and extreme events influence the structure and function of ecosystems worldwide, jointly with plant invasion (Vitousek et al., 1997; Parmesan and Yohe, 2003; Kelly and Goulden, 2008). By altering the dominant perennial plant cover, increasing resource availability and opening space for colonization, disturbance facilitates the arrival and dispersal of invasive species (Pierce et al., 2013; Herben et al., 2018), which are often characterized by competitive functional traits such as larger size, increased fecundity and faster germination than native species (Callaway and Ridenour, 2004). Invasive plants benefit disproportionately from disturbance (Smith and Knapp, 1999) and, notably in grasslands, they can act as drivers of change (Vitousek et al., 1997), shifting ecosystems to alternative stable states that are less diverse and dominated by alien species (Gibbons et al., 2017). However, some studies highlighted that their performance may not differ from dominant native species (Sheppard et al., 2012).
The warty cabbage, Bunias orientalis L. (Brassicaceae), benefits from excessive disturbance, copes very well with mowing due to rapid rosette regrowth and increased seedling recruitment (Woitke and Dietz, 2002) and forms tall dense stands that successfully compete with native grasses for sunlight, nutrients, and pollinators (Birnbaum, 2006). Over the last four decades the species has become highly invasive in various parts of Northern and Central Europe, including German grasslands (Dietz et al., 1996, 1999; Woitke and Dietz, 2002). In this region, grasslands account for more than a quarter of farmed land, with more than half of all plant species found in the country depending on the habitat. However, in recent decades they have been under pressure, with a decline by 12% from over 5.3 million hectares reported in 1991 to 4.7 m ha nowadays (Umweltbundesamt, 2020).
In this study, we focus on how invasion success of B. orientalis in native grassland communities in Germany may change with varying hydrological conditions (ranging from very dry to waterlogged by adjusting water table depth) that are expected under climate change. We conducted a 3-year mesocosm experiment in a common garden addressing the following research questions: (1) Does the establishment and growth of B. orientalis differ among water table depths? (2) Does the effect of water table depth depend on the presence and biomass of the native grassland community?
Materials and Methods
Study Species
Bunias orientalis is a tall (up to 1.2 m height) polycarpic biennial or perennial hemicryptophyte of high dispersal ability that may live up to 10 years or even longer; it grows as a semi-rosette with large leaves and numerous little flowers. The species is hermaphroditic and insect-pollinated, with a self-fertile breeding system (Dietz et al., 1999), but it can also reproduce vegetatively by root fragments (Bąba and Kompała-Bąba, 2008). B. orientalis has a high reproductive effort (from 15 up to 45% of reproductive biomass i.e., g dry weight of reproductive biomass per g aboveground biomass), high germination rates (up to 60%) and a high potential for vegetative growth following root fragmentation (Steinlein et al., 1996). Moreover, it has a persistent seed bank, with large seeds (mean seed mass 7 mg, Dietz et al., 1999) occurring in densities from 1,000 to 15,000 seeds/m2, able to be viable for more than 3 years (Steinlein et al., 1996).
The native range is Caucasus and southern Russia, where the species occurs in grasslands, sunny edges of forests, dappled shade and riverbanks. There, the species requires moist soils (Clapham et al., 1962). Multiple independent introductions in the 18th century brought B. orientalis to Europe where it rapidly became a dominant invasive species in many countries, including Germany, Czech Republic, Poland, Sweden, Norway, and elsewhere (Harvey et al., 2010). In other neighboring countries (France, Great Britain, Netherlands) the species is not yet considered invasive, although it occurs as an established neophyte. In the invaded range B. orientalis is highly versatile and easily establishes in a variety of semi-natural or disturbed habitats such as roadside verges, railways, fallow lands, floodplain meadows, pastures, ruderal sites, and even gardens (Birnbaum, 2006). In the invaded range the species is more tolerant to various soil conditions although it prefers open, nutrient rich clay or sand soils of a neutral pH and does not grow under shaded conditions. From these sites it can invade dry grasslands, especially neglected dry meadows (Birnbaum, 2006). Moderate disturbance caused by mechanical damage (e.g., mowing) or herbivore damage (e.g., slug grazing) promote the survival and establishment of the species (Bąba and Kompała-Bąba, 2008).
Experimental Design
To study the effects of hydrological stress on the establishment and growth of the invasive plant B. orientalis, we set up a mesocosm experiment in a common garden (48°71′ N, 9°20′ E, 389 m a.s.l.) at the University of Hohenheim in Stuttgart, Germany. The climate is oceanic, subtype subcontinental, mild, with no dry season and warm summers. The long-term average annual temperature is 9.4°C and annual precipitation is 718 mm (Agrarmeteorologie Baden-Württemberg, 2019). The experiment was conducted from April 2016 to November 2018 and included five hydrological treatments (chronic drought, dry, mesic, wet, waterlogged), applied to bare soil (simulating disturbance) and grassland community pots.
Naturally composed mature grassland communities were dug out in November 2015 from four typical hay meadows (Arrhenatherion elatioris), which all belonged to the same organic farm property in South-Western Germany (48°53′ N, 8°54′ E, 290–380 m a.s.l.). These dug-out communities (including soil, roots and the entire grassland community, with a soil depth of 15–20 cm) were placed in 20-L pots (28 cm × 35 cm ø), which were previously filled with a layer of sandy loam at the bottom. The communities thus had different species compositions (made up of mostly perennial grasses, forbs, and legumes), but provided a more natural environment to study invasion success. The communities contained on average 7.2 species at the start of the experiment in 2016, with the most common species being the grasses Arrhenatherum elatius (L.) P.Beauv. ex J. Presl & C. Presl., Festuca pratensis Huds., and Poa pratensis L. (Supplementary Table S1). The bare soil pots were entirely filled with the same sandy loam used at the bottom of the grassland pots. All pots were then kept in the greenhouse until April 2016, when they were transferred to the common garden and placed inside large 260-L pools (Supplementary Figure S1). Each pot was placed in a separate pool to avoid pseudo-replication (with the exception of one pot of bare soil, which shared a pool with one community pot). The pools also contained some other pots, which however are not part of the experiment described here. Seeds of B. orientalis were sown on 30 June 2016 in 50 pots, of which 40 were with communities (8 replicates per water table depth treatment), and 10 control pots without (bare soil, 2 replicates per treatment). Within the logistical limitations of our experiment, we allocated more replicates for the community treatments as we expected lower establishment success in the grassland. In each pot, 12 seeds were sown, with a total number of 600 seeds.
We aimed to mimic a realistic scenario with natural variation in precipitation, applying different soil moisture conditions on these near-natural grassland communities, ranging from waterlogged, over wet, mesic, dry to chronic-drought-exposed communities. We achieved the desired hydrological regimes by adjusting the water table depth in the pools to five levels (Supplementary Figure S2). In the waterlogged treatment, the water table was kept at −5 cm below the soil surface, in the wet treatment at −15 cm and in the mesic treatment at −25 cm. The water table depth was kept constant by watering the pools twice per week and preventing higher water levels than desired with holes in the pools made at the respective height (Supplementary Figure S2; see also Rai et al., 2018; Walter, 2020). In the dry treatment, pools contained no water (i.e., holes at the bottom) and pots received natural rainfall. Under chronic drought conditions, precipitation was additionally reduced by 30% with a partial rainout shelter, using curved, transparent PVC stripes mounted on a wooden construction that covered 30% of the area above the pools (Supplementary Figures S1, S2).
The year 2016 was characterized by an exceptionally wet June (115 mm rainfall compared to the long-term 30-year average (1981–2010), mean of 87 mm), followed by an exceptionally dry period from July to September (only 117 mm rainfall compared to 212 mm in the long-term mean) (Agrarmeteorologie Baden-Württemberg, 2019). 2017 received almost 130 mm more rainfall than the long-term during the growing season (from April until November), with June and July being especially moist months (+ 67 mm). 2018 had a record-breaking dry and hot summer (+ 2.1° and 120 mm less precipitation than the long-term average, from April until November) (Agrarmeteorologie Baden-Württemberg, 2019). As expected, soil moisture differed among the applied hydrological treatments (see Walter, 2020 for details on average volumetric soil water content).
During the first year, germination of B. orientalis seedlings was monitored at weekly intervals until the end of October. In each year, number of B. orientalis individuals were counted in late May or beginning of June and at the end of October, after which all plant material (B. orientalis and the community) was cut 2 cm aboveground (mimicking extensive agricultural regimes). In each October, aboveground biomass of B. orientalis and the grassland communities were harvested, dried at 60° for 4 days and weighed.
Data Analysis
Statistical analyses were performed with R 3.6.1 (R Core Team, 2019) using the lme4 R package (Bates et al., 2015). For those seeds that germinated during the first season (2016), we used a linear mixed effects model to test whether time of germination (i.e., week after sowing, up to week 14 referring to the week of harvest) was affected by water table depth (factor with 5 levels: chronic drought, dry, mesic, wet, waterlogged) and the presence of the community (2 levels: community, bare soil) and their interaction. Pot identity (factor with 50 levels) was included as a random effect. Marginal and conditional R2 was calculated using the MuMIn package (Barton, 2020).
For the analysis of number of individuals per pot over the 3 years, a generalized linear mixed model was employed with a Poisson distribution. The temporal (pseudo-)replicates of data-assessments were used as a random effect (5 levels: October 2016, May 2017, October 2017, June 2018, October 2018) as well as pot identity to account for repeated measures on the same pot. For (log-transformed) aboveground biomass, a linear mixed effects model was applied, using timing of harvest as a random effect (3 levels: October 2016, October 2017, October 2018). Note that in these models, due to singular fit issues, we were not able to account for pot identity. Water table depth and community as well as their interaction were used as fixed effects. In a first step, we tested whether the interaction between water table depth and presence of the community was significant (tested using likelihood ratio tests with a chi-squared test statistic). If the interaction was significant, separate models for each community type were employed in a second step. For the pots with the community, we then additionally tested whether community biomass affected B. orientalis performance, adding this as a fixed effect to the above-mentioned models.
Results
Effect of Water Table Depth and Community on Germination of Bunias orientalis
The percentage of germinated seeds of Bunias orientalis in 2016 was higher in bare soil (53% i.e., 64/120) compared to community pots (15% i.e., 72/480). The effect of water table depth on germination time was not significantly affected by the presence of the native grassland community (i.e., no significant interaction, Table 1).
Table 1. Linear mixed effect models for germination time of Bunias orientalis in the first season (2016) and biomass over 3 years (2016–2018), and generalized linear mixed model for number of individuals over 3 years.
However, seeds in bare soil pots germinated 3 weeks (on average) earlier than seeds in the community (Table 1 and Figure 1). Time of germination was significantly affected by water table depth (Table 1), with an earlier germination in the wet treatment (mean germination time 5.95 ± 0.51 week after sowing, Figure 1) followed by the mesic and waterlogged treatments (mean 6.98 ± 0.52 and 7.20 ± 1.74 week, respectively). Notably, seeds in the dry (mean 8.18 ± 1.01 week) and chronic drought treatments (mean 8.78 ± 1.12 week) germinated on average 2–3 weeks later than seeds in the other treatments, irrespective of whether they were growing in bare soil pots or communities.
Figure 1. Germination time in weeks after sowing of Bunias orientalis during the first season (2016) depending on water table depth treatment in the community (gray bars, n = 5, 3, 45, 34, and 7 individuals) and empty pots (white bars, n = 9, 14, 23, 22, and 3 individuals). Boxplots show the median per group (solid line), boxes represent the 25th and 75th quantile, whiskers the normal data range and circles the outliers.
Effect of Water Table Depth and Community on Number of Established Individuals
The number of established individuals decreased over time: 136 seeds had germinated by October 2016, whereas 73 individuals (51 in bare soil, 22 within the community) were recorded in October 2017 and only 8 individuals (7 in bare soil pot, 1 within community) survived until October 2018 by the end of the experiment (Supplementary Figure S3).
The effect of water table depth on the number of individuals did not depend on whether plants were growing in the community (Table 1, Figure 2, and Supplementary Figure S3). Indeed, both in the community and in bare soil pots, the number of individuals significantly differed among water table depth (Table 1 and Figure 2). Most individuals established in mesic conditions and bare soil pots (mean 5.8 ± 1.6).
Figure 2. Number of Bunias orientalis individuals established per pot (from initially 12 sown seeds) over 3 years (2016–2018) depending on water table depth treatment in the community (gray bars, n = 40 each) and empty pots (white bars, n = 10 each). Boxplots show the median per group (solid line), boxes represent the 25th and 75th quantile, whiskers the normal data range and circles the outliers.
In communities, the number of individuals was also affected by community biomass [χ2 (1 df) = 6.53; p = 0.011], which ranged between 0.29 and 130.48 g, with an average of 35.69 g/pot. The highest number of individuals that established per pot were observed in native grassland communities where community biomass was lower than the average (i.e., 10, 8, and 7 individuals/pot established respectively in community biomass of 17.57, 28, and 17.73 g), with a general trend of individuals having successfully established in communities with a biomass lower than 80 g (Supplementary Figure S4).
Effect of Water Table Depth and Community on Plant Biomass
The effect of water table depth on aboveground plant biomass significantly depended on whether plants were growing in the community (Table 1, Figure 3, and Supplementary Figure S5). Both in the community and in bare soil pots plant biomass differed among water table depth (Table 1 and Figure 3). In communities, the species reported a significantly higher biomass in mesic (mean 0.051 ± 0.021 g) and wet conditions (0.047 ± 0.018 g), however community biomass did not affect B. orientalis biomass [χ2 (1 df) = 0.031; p = 0.86]. Conversely, biomass of B. orientalis observed in bare soil was the highest in pots that received only natural rainfall, i.e., the dry treatment (1.571 ± 0.783 g, Figure 3), followed by the mesic treatment (mean 1.153 ± 0.737 g). We noted that B. orientalis never flowered during the experiment.
Figure 3. Aboveground biomass of Bunias orientalis over 3 years (2016–2018) depending on water table depth treatment in the community (gray bars, n = 24 each) and empty pot (white bars, n = 6 each). Boxplots show the median per group (solid line), boxes represent the 25th and 75th quantile, whiskers the normal data range and circles the outliers. The y-axis is shown on a log-scale.
Discussion
Establishment and Growth of Bunias orientalis in Bare Soil and Native Grassland Communities
In contrast to its previously demonstrated invasiveness (Steinlein et al., 1996; Dietz and Steinlein, 1998; Dietz et al., 1999; Woitke and Dietz, 2002; Birnbaum, 2006), the overall performance of Bunias orientalis in our experiment was rather low, with less than 23% of seeds having established after the first season and just 8 individuals surviving at the end of the experiment. Previous studies already reported a low germination rate (20%) in ruderal sites characterized by low intensity of disturbance (mowing) and soil deposition, whereas germination reached the highest rates (60.1%) in nitrogen rich, shady and moist soil (Steinlein et al., 1996). Probably competition by shading was too high in the still intact communities in 2016 (height of communities ranged between ca. 10–30 cm and cover between 80 and 100%) to allow for high germination rates. Moreover, the exceptionally dry period in mid-summer 2016 and the record-breaking dry and hot summer of 2018 could have impacted negatively on seed germination and early seedling establishment, a phase demonstrated to be the most critical for water stress and plant survival (Ahmad et al., 2009).
The low performance of B. orientalis was also reflected in the finding that plants never flowered during the experiment, although the species normally flowers in the second year or later (Bąba and Kompała-Bąba, 2008). However, plants that can grow either biennially or perennially may use different strategies depending on the conditions they grow in: the reduced performance of plants may have allowed for a retention of accumulated resources for perennation (Miao and Bazzaz, 1990) and therefore selectively favored perennial plants (Steinlein et al., 1993).
In addition to the overall low performance, B. orientalis performance was clearly constrained by interspecific competition with the native grassland community. Other studies also showed higher growth of B. orientalis in the absence of competition, such as higher biomass (Koorem et al., 2018), higher cumulative leaf lengths of the species and higher seed numbers (Dietz et al., 1999). Reducing total cover of all other species, Kiełtyk (2014) demonstrated that B. orientalis cover in meadows increases as a consequence. Given that we used natural dug-out mature communities, competition was high because communities were already well established. Light competition from taller species might be a limiting factor in the establishment of the species (Dietz et al., 1996). Indeed, community biomass affected how many individuals established over the years, but notably it did not with regard to B. orientalis biomass, whereby either fewer individuals formed the classic large rosettes occupying the given area or more individuals remained smaller. To compensate for its low competitive ability compared with other ruderal forbs (Dietz et al., 1998; Birnbaum, 2006), B. orientalis has been shown to use other strategies to successfully invade: it requires moderate disturbance to establish, that facilitates invasion by reducing competition and changing resource conditions in favor of one species over another (Hager, 2004; Domènech and Vilà, 2008). For instance, formation of molehills which damages resident vegetation and creates open areas of bare soil, leading to less-compacted soil and vegetation with a lower-density rhizosphere, facilitates invasion of B. orientalis (Kiełtyk and Mirek, 2015). In contrast, mimicking standard management practices in extensively used semi-natural grasslands in our study, with mowing twice a year, did not favor the establishment, survival and potential invasiveness of the plants, maybe because the degree of disturbance was too low. However, simulating a high degree of disturbance with the bare soil pots greatly increased performance of B. orientalis.
Effect of Hydrological Stress on Bunias orientalis Performance
The different soil moisture conditions that we created by adjusting water table depth, simulating wetness, temporary flooding and especially dryness strongly influenced the performance of the plants. Seed germination in the first season occurred earlier and the number of established individuals as well as biomass production over the following years was generally higher in the wet and mesic treatments. Indeed, even though B. orientalis exhibits a wide ecological tolerance, previous studies showed that the species establishes better in moist soils (Clapham et al., 1962; Steinlein et al., 1996).
Notably, B. orientalis showed greater performance and a wider ecological tolerance along the hydrological gradient in bare soil than in the community, with competition with the surrounding vegetation influencing the establishment and growth of the species. In particular, while establishment was highest in mesic and wet conditions regardless of the community, the presence of the community mostly limited plant growth to mesic and wet conditions. In contrast, plant biomass production in bare soil was not restricted to the non-stressful hydrological conditions, with the highest biomass found in dry condition, but moderate performance also observed in wetter treatments. This finding suggests that the smaller number of individuals on average established in dry treatments compensated for their number by producing more biomass. We note some limitation with the interpretation of the biomass results, however, because due to the limited number of pots in our experiment, we could not fully statistically account for non-independence among repeated measurements. Nevertheless, there are some likely explanations for our results. Reduced intraspecific competition might have favored faster growth rates in the dry treatments. In contrast, despite the lower aboveground biomass in dry communities, belowground competition for water might have become more severe, as found in other experimental studies (e.g., Walter, 2018). This may have limited plant growth of B. orientalis seedlings in interspecific competition under such resource stress, especially since seedlings usually have a smaller root system than established plants. The generally lower success of plants in waterlogged conditions (whereby differences between bare soil pots and community were less pronounced) may be attributed to anaerobic stress rather than increased competition, because special adaptations are necessary to cope with anoxia, as has been shown in other studies (Jung et al., 2009; Bartelheimer and Poschlod, 2016).
The results of our study have implications regarding possible changes in the dynamics between native and the invasive species in the future, based on the timing and frequency of precipitation patterns: the establishment of B. orientalis seedlings might turn into a successful invasion only if germination of seeds will occur in moderate precipitation conditions, followed by drought conditions coupled with disturbance. Therefore, rainy and wet springs and warmer summers might help the invasion success of this species, particularly if a disturbance creates patches of bare soil.
Conclusion
We conducted a 3-year mesocosm experiment in a common garden focusing on the invasion success of the warty cabbage Bunias orientalis in German native grassland communities. Thereby we compared the establishment and growth of plants in such communities with bare soil in varying hydrological conditions (from waterlogged to dry soil moisture), mimicking predicted changes in precipitation patterns under climate change. Establishment and biomass of B. orientalis differed among water table depth, with higher performance in wet and mesic conditions. However, despite its wide ecological tolerance in the absence of competing plants, invasion success of B. orientalis in the native grassland communities was generally low, which might be due to the low competitive ability of the species in conditions of hydrological stress and the fairly low degree of disturbance in our near-natural grasslands. Our results suggest that with changing of precipitation patterns toward more extreme events with frequent and pronounced waterlogged and drought conditions, the establishment of B. orientalis within grassland communities might be reduced. However, within patches of bare soil, this will not occur, where disturbance combined with drought will favor species establishment, survival and even invasiveness, a scenario which should be further tested in future studies.
Data Availability Statement
The raw data supporting the conclusions of this article will be made available by the authors, without undue reservation.
Author Contributions
JW and CS designed the study. AC and JW collected the data. AC and CS performed the analyses. AC wrote the first draft of the manuscript. All authors contributed substantially to the revisions.
Funding
This work was supported by the German Research Foundation (DFG, WA 3442/2-1 and SH 924/1-1).
Conflict of Interest
The authors declare that the research was conducted in the absence of any commercial or financial relationships that could be construed as a potential conflict of interest.
Supplementary Material
The Supplementary Material for this article can be found online at: https://www.frontiersin.org/articles/10.3389/fevo.2021.625587/full#supplementary-material
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Keywords: Bunias orientalis, common garden experiment, grassland, hydrological gradient, interspecific competition, plant invasion, precipitation changes
Citation: Corli A, Walter J and Sheppard CS (2021) Invasion Success of Bunias orientalis (Warty Cabbage) in Grasslands: A Mesocosm Experiment on the Role of Hydrological Stress and Disturbance. Front. Ecol. Evol. 9:625587. doi: 10.3389/fevo.2021.625587
Received: 03 November 2020; Accepted: 01 March 2021;
Published: 18 March 2021.
Edited by:
Justin S. H. Wan, Jiangsu University, ChinaReviewed by:
Dima Chen, China Three Gorges University, ChinaShaokun Wang, Chinese Academy of Sciences (CAS), China
Copyright © 2021 Corli, Walter and Sheppard. This is an open-access article distributed under the terms of the Creative Commons Attribution License (CC BY). The use, distribution or reproduction in other forums is permitted, provided the original author(s) and the copyright owner(s) are credited and that the original publication in this journal is cited, in accordance with accepted academic practice. No use, distribution or reproduction is permitted which does not comply with these terms.
*Correspondence: Christine S. Sheppard, Y2hyaXN0aW5lLnNoZXBwYXJkQHVuaS1ob2hlbmhlaW0uZGU=
†These authors have contributed equally to this work