Haihao Yu
Xianru Dong†
Chunhua Liu
Shufeng Fan- The National Field Station of Freshwater Ecosystem of Liangzi Lake, College of Ecology, Wuhan University, Wuhan, China
When exotic species are introduced into new areas, establishment is a vital step in their invasion process. Therefore, overwintering strategies determine whether an exotic species from low latitudes can successfully invade middle- and high-latitude areas. In this study, we investigated the effects of nutrient and water drawdown on overwintering in an exotic aquatic plant from the tropical zone, Eichhornia crassipes, at the northern margin of its distribution in China. The population density, size of individuals, and the size and nitrogen concentration of overwintering organs (stem base) of E. crassipes that grew in high-nutrition water were greater than those that grew in low-nutrient water before winter. The overwinter survival rate of E. crassipes was significantly affected by the water level and nutrient. The thick and dense floating mat of E. crassipes can increase the temperature of water bodies; therefore, the overwinter survival rate of E. crassipes was higher in constant-water-level and high-nutrient treatment. In contrast, due to the loss of heat preservation provided by the floating mats and the low nitrogen concentration in the stem base, all individuals of E. crassipes died in constant-water-level and low-nutrient treatment. In the water-drawdown treatments, the stem base of E. crassipes was directly exposed to low-temperature air; therefore, the overwinter survival rate of E. crassipes was lower. Our results reveal that eutrophication can not only improve the competitiveness of E. crassipes but can also improve the survival rate of overwintering plants in temperate regions. Our study also suggests that removing nutrients from the water and regulating the water level can limit the invasion of E. crassipes in temperate and subtropical regions.
Introduction
When exotic species are introduced to new ranges, only a few species can establish populations and become invasive. Propagule pressure and the self-sustaining ability of species in adverse environments mainly influenced the establishment (Williamson and Fitter, 1996a; Williamson and Fitter, 1996b). In high-altitude and high-latitude regions, overwintering abilities and strategies are critical for the establishment, distribution, and spread of exotic species, especially for species that originated from habitats in warmer regions. Studies of the overwintering ability of species and factors that affect overwintering allow us to clarify the mechanisms of invasion and better control them.
Overwintering is the process by which some organisms pass through or wait out the winter season. During this period, organisms experience numerous kinds of abiotic (cold or sub-zero temperatures, frost, frost heave, ice, snow, low precipitation, drought) and biotic (limited food supplies, low-temperature fungi, and bacteria) stresses, making normal activity or even survival difficult or near impossible (Bertrand and Castonguay, 2003). Temperature is a limiting factor for survival, growth, and reproduction in plants and many animals (Woodward, 1987; Charnov and Gillooly, 2003). Low-temperature and freezing events in winter result in the invasion failure of many introduced exotic species or restrict the distribution ranges of species that have successfully invaded (Owens et al., 2004; Walther et al., 2009; MacIsaac et al., 2016). Although climate warming causes exotic species to invade regions within which they could not survive before, extends their temporal and spatial distribution, and increases their performance (Walther et al., 2002; Hellmann et al., 2008; Walther et al., 2009; Chown et al., 2012; Concilio et al., 2013; Sorte et al., 2013), the ranges of some exotic species may also be reduced (Merow et al., 2017). In some ranges, precipitation was also low in winter, which leads to a decline in the water levels of lakes and rivers. Water level is an important factor affecting the growth and reproduction of aquatic plants in freshwater ecosystems (Chambers and Kalff, 1985; Ishii and Kadono, 2004; Deegan et al., 2006; Smith and Brock, 2007; Xiao et al., 2007; Xie et al., 2008). Moreover, water is usually considered to be a temperature buffer to prevent aquatic plants from direct damage by freezing in winter (You et al., 2013). Therefore, water level changes can also influence the overwintering of exotic species.
Nutrients are also another important abiotic factor affecting species growth, propagation, or colonization, and as one of the results of global changes that is driven by human activities and rapid economic growth, eutrophication has become increasing common and severe in water systems (Ryther and Dunstan, 1971; Smith et al., 1999). Previous studies found that the relative growth rates, reproductive rates, photosynthetic rates, leaf nitrogen contents, and photosynthetic nitrogen-use efficiencies of aquatic exotic plants increase more intensively with increasing nutrient availability than those of native species (Xie et al., 2010; Fan et al., 2013). However, few studies have examined the effects of eutrophication on the overwintering of exotic plants. With the intensification of global change, water level fluctuation (e.g., floods and droughts) will become more intense and frequent, and eutrophication will also be more severe and widespread in freshwater ecosystems (Arnell and Reynard, 1996; Allen et al., 2001; Schindler, 2006). Studies the effects of water level changes and eutrophication on the overwintering of exotic aquatic plants can help to predict and manage exotic aquatic plants.
One of the world’s most prevalent invasive aquatic plants, Eichhornia crassipes (water hyacinth), is a free-floating and mat-forming aquatic plant that originates in tropical South America. Now, E. crassipes has invaded over 50 countries on five continents (Villamagna and Murphy, 2010). It occurs in various freshwater ecosystems (estuaries, rivers, lakes, ponds, reservoirs, and canals); forms thick, extensive mats; and causes severe ecological and socio-economic changes in where it has invaded (Mitchell, 1985; Center, 1994). E. crassipes reproduces both sexually and asexually. In invaded regions, it increases in population size mainly through vegetative reproduction, forming new ramets from axillary buds on stolons produced through the elongation of internodes (Center and Spencer, 1981). Sexual reproduction rarely occurs, owing to the lack of suitable pollinators and appropriate sites for germination and seedling establishment in invaded regions (Barrett, 1980). Temperature and water nutrient levels are key factors that affect the invasion of E. crassipes (Wilson et al., 2005). The optimal growth temperatures for water hyacinth are 28–30°C; growth stops if the water temperature falls below 10°C or rises above 40°C (François, 1969; Gopal, 1987), and the plant dies when it experiences prolonged cold temperatures below 5°C (Gopal, 1987; Owens and Madsen, 1995). The edge of the distribution of E. crassipes occurs where the mean temperature in January is 1°C, the mean annual temperature is 13°C, and the average lowest temperature during the year is −3°C (Ueki et al., 1976). The distribution of E. crassipes is considered to be limited to tropical or subtropical regions because it cannot overwinter in environments with extreme cold temperatures or ice cover (Aurand, 1982; Tyndall, 1982; Madsen et al., 1993). However, some researchers have predicted that its distribution may expand into higher latitudes as temperatures rise (Rodríguez-Gallego et al., 2004; Hellmann et al., 2008; Rahel and Olden, 2008). The growth and reproduction of E. crassipes are closely related to the nutrient level of water bodies (Reddy et al., 1989; Reddy et al., 1990; Xie et al., 2004). Some studies found that a high-nutrient supply can improve the photosynthetic capacity, resource-use efficiency, and competitiveness of E. crassipes (Ripley et al., 2006; Fan et al., 2013). In addition, both the depth of the water and changes in water level are important in the growth of E. crassipes (Téllez et al., 2008). For example, the results of study of Oki and Ueki (1984) indicated the leaf area and growth rate of E. crassipes in shallow water were higher than those in deep water, while more roots were found in the latter. Moreover, some researchers have found fluctuations in water level promoted the invasion of E. crassipes (Freidel et al., 1978; Téllez et al., 2008).
Eichhornia crassipes was introduced into China as an ornamental plant in the early 1900s and is now widely distributed in 17 provinces or cities and causes severe damage in more than 10 provinces. In tropical China, water hyacinth can grow all year round. In subtropical regions, the plant dies back in winter and sprouts new plants from axillary buds on the stem base the following year (Gao, 2005). In the middle and lower reaches of the Yangtze River, the overwintering survival rate of water hyacinth is very low (Gao, 2005). However, we knew little about the overwintering mechanisms of water hyacinth (You et al., 2013; Liu et al., 2016). In order to test whether eutrophication and water level changes can facilitate the overwintering of E. crassipes as well as climate warming and found the reasons, we investigated the effects of nutrients and water drawdown on the overwintering of E. crassipes, at the northern margin of its distribution in China. We attempted to address the following questions: (i) Do high nutrient levels affect the performance of E. crassipes? (ii) Do different treatments lead to different overwintering temperatures of E. crassipes? (iii) Can high nutrient levels or water cover increase the overwintering survival rate of E. crassipes?
Materials and Methods
Study Site
The experiment was conducted at The National Field Station of Freshwater Ecosystem of Liangzi Lake, Wuhan University, China (30°05′−30°18′N, 114°21′–114°39′E). Liangzi Lake is a shallow lake with an area of 304.3 km2 in the central reaches of the Yangtze River basin. The climate of this area is a typical subtropical climate. The average temperature in winter ranges from 3 to 7°C, which is the critical temperature for the overwintering of E. crassipes; therefore, Liangzi Lake is located at the northern margin of the E. crassipes distribution in China (Li and Xie, 2002).
Experimental Design
In early July 2015, E. crassipes plants were collected from the bay of Liangzi Lake and cultivated in a 4 × 4 × 4-m concrete pool. Fifteen days later, 240 healthy plants of similar size (mean fresh biomass 63.56 ± 5 g, mean height 14.28 ± 3 cm, mean leaf number 12 ± 3) were transferred to 24 concrete pools (length: 2 m, width: 2 m, depth: 1.5 m) filled with approximately 10 cm of lake sediment (from Liangzi Lake, N:P = 2.35:0.014 mg/L) and 120 cm of water (from Liangzi Lake, N:P = 0.6:0.05 mg/L); each pool was planted with 10 plants. The whole experiment lasted about 35 weeks, from July 20, 2015, to April 12, 2016, and was divided into two stages (Figure 1). During the first stage (growing stage, from the beginning of the experiment to December 1, 2015), the pools were divided into two treatments: low nutrients and high nutrients, and each nutrient level had 12 replicates (n = 12). During the second stage (overwintering stage, from December 2, 2015, to the end of the experiment), a water level factor was added to half of the pools in those two treatments until the experiment finished; there were therefore four treatments during this stage: 1-1: low nutrients and water drawdown; 1-2: low nutrients and a constant water level; 2-1: high nutrients and water drawdown; and 2-2: high nutrients and a constant water level. Each treatment had six replicates (Figure 1).
Figure 1 Diagram of the experimental design (the number following the “×” indicates the number of replicates. One plant in diagram represents 10).
During the growing stage, in the high-nutrient treatment, we increased the total nitrogen (TN) and total phosphorus (TP) concentrations to 20 mg/L N and 1.0 mg/L P by adding KH2PO4, NH4NO3, and 10% Hoagland solutions to the lake water. In the low-nutrient treatment, only 10% Hoagland solution was added to the lake water. To maintain a relatively constant concentration of the culture solution, an appropriate amount of nutrients was added into relevant pools every half month after the nutrient level was measured. At the end of the growing stage, the temperature dropped with the onset of the yellowing of leaves, causing the plants to stop growing. Then, the experiment entered the second stage (overwintering stage). In the water-drawdown treatments, the water was drained (no water over sediment) by pump. In constant water level treatments, the water level was kept in line with that of the first stage. And the water levels of each treatment after rain were maintained by pumping. No nitrogen phosphorus fertilizer was added to each treatment during the second stages, because the plants have stopped growing. To study question (ii), do different treatments lead to different overwintering temperatures of E. crassipes? the temperature of the microenvironment in which the plants were located was monitored at 30-min intervals with four automatic thermometers during the overwintering stage. These thermometers were placed in four pools selected randomly from the four different treatments. In the water-drawdown treatments, the thermometer probes were placed closed to the stem base of the water hyacinth. In the treatments with a constant water level, the thermometer probes were placed in the surface layer of water (5 cm from the surface of the water) where the stem base of the water hyacinth was occurred.
Data Collection
To answer question (i), do high nutrient levels affect the performance of E. crassipes? we counted the plants in each pool and harvested three plants randomly from each pool to measure the traits before winter at the end of the growing stage. The length and diameter of the stem base were measured with a Vernier caliper. The biomass of the plants and the stem base were obtained after drying plants in an oven at 70°C for 72 h to a constant weight. The soluble sugar and starch concentrations of the stem base were measured by the sulfuric acid anthrone colorimetric method described by Hansen and Moller (1975). The nitrogen and carbon concentrations of the stem base were analyzed by a FLASH 2000 Organic Elemental Analyzer (Thermo Fisher Scientific Inc., USA).
To answer question (iii), can high nutrient levels or water cover increase the overwintering survival rate of E. crassipes? we counted the number of surviving plants (with the original plant and its new ramets counted as one plant) approximately every 10 days from early March 2016 (when some plants began to regrow) to April 12, 2016 (when the weather became warm enough to ensure that all plants with survival potential survived successfully). In addition, we identified the plants with new green leaves as those that had survived. The final survival rate was calculated as the number of plants that had survived divided by the number of plants at the end of the growing stage.
Data Analysis
To answer question (i), do high nutrient levels affect the performance of E. crassipes? One-way ANOVA was performed to examine the effects of nutrients on plant number, plant biomass, stem base biomass, stem base length, stem base diameter, and the soluble sugar concentration, starch concentration, carbon concentration, and nitrogen concentration in the stem base. To test question (ii), do different treatments lead to different overwintering temperatures of E. crassipes? the differences in the mean temperatures of the microenvironment in which the stem bases of the plants were located among the different treatments were also tested by one-way ANOVA. To answer question (iii), can high nutrient levels or water cover increase the overwintering survival rate of E. crassipes? number of plants after the winter was tested with a general linear model (Poisson distribution), which indicated that both the nutrient level and water level significantly impacted the number of surviving plants. Then, two-way ANOVA was used to test the impacts of nutrient level and water level in winter and their interaction effect on the survival rate and number of surviving plants after winter. The survival rate, length and weight of the stem base, number of plants before winter, and soluble sugar concentration of the stem base were transformed using the SQRT function to ensure the homogeneity of the variance or a normal distribution of the residuals before the analysis. All data were analyzed with SPSS 19.0 software (SPSS, Chicago, IL, USA).
Results
Growth Traits During the Growing Stage
Nutrient addition significantly and positively affects the populations of E. crassipes and the performance of the overwintering stem base (question i). The number of E. crassipes plants in the high-nutrient treatments was higher than those in the low-nutrient treatments (Figure 2A, F=219.227, P < 0.001). Biomass of single plants in the high-nutrient treatments was also higher than those in the low-nutrient treatments (Figure 2B, F = 19.625, P < 0.001). The population of E. crassipes in the high-nutrient treatments covered the whole surface of the water and formed dense, interlocking mats; the mean density reached 152 ind/m2. However, in the low-nutrient treatments, weaker plants were scattered on the surface of the water, and the mean density of E. crassipes was 21.23 ind/m2. The biomass, length, and diameter of the stem base in the high-nutrient treatments were all higher than those in the low-nutrient treatments (Figures 2C–E; Fbiomass = 36.722, Flength = 38.491, Fdiameter = 51.417; Pbiomass < 0.001, Plength < 0.001, Pdiameter < 0.001). The high nutrient level also significantly increased the N concentration in the stem base (Figure 3A, F = 13.562, P < 0.01). But the C concentration, C/N ratio, and soluble sugar concentration in the low-nutrient treatments were higher than those in the high-nutrient treatments (Figures 3B–D; FC = 19.353, FC/N = 21.358, F sugar = 26.571; PC < 0.001, PC/N < 0.001, P sugar <0.001). There was no difference in the starch concentration between the high- and low-nutrient treatments (Figure 3E, F = 0.002, P > 0.05).
Figure 2 Number (A), biomass (B), stem base biomass (C), stem base length (D), and stem base diameter (E) (mean ± SD) of Eichhornia crassipes under different nutrient treatments before winter. Significant differences among the treatments are indicated by different letters at P < 0.05.
Figure 3 N concentration (A), C concentration (B), C/N ratio (C), soluble sugar concentration (D), and starch concentration (E) (mean ± SD) in the stem base of Eichhornia crassipes under different nutrient treatments before winter. Significant differences among the treatments are indicated by different letters at P < 0.05.
Microenvironment Temperature and Survival Traits During the Overwintering Stage
In winter, the temperatures of the microenvironments in which the stem bases of the plants located were different (question ii). The mean temperature and minimum temperature of the water around plants in the constant-water-level treatments were higher than the mean temperature and minimum temperature of the air near the plants in the water-drawdown treatments (Table 1). In contrast, the maximum temperatures were higher in the latter treatments. In the constant-water-level treatments, the mean temperature and minimum temperature in the high-nutrient treatment were higher than those in the low-nutrient treatment (Table 1). In water-drawdown treatments, the mean temperature and minimum temperature under high nutrient level were lower than those under low nutrient level (Table 1).
Table 1 Microenvironment temperature in winter. Significant differences among the treatments are indicated by different letters at P < 0.05.
The final survival rate and total number of plants after overwintering were significantly affected by affected by nutrient level, water level, and their interaction (Table 2) (question iii). The high-nutrient treatments increased the survival rate and number of E. crassipes plants after overwintering (Table 2, Figures 4A, B). Under the high-nutrient conditions, water drawdown in winter significantly decreased the survival rate and total number of E. crassipes plants after overwintering (Figures 4A, B). E. crassipes in the high-nutrient and constant-water-level treatment exhibited the highest survival rate (4.71 ± 3.69%) and number of surviving plants (31 ± 25.84), which were markedly much higher than those in the other three treatments, and there were no significant differences in survival rate among the other three treatments. It is worth noting that all the plants died in the low-nutrient and constant-water-level treatment (Figures 4A, B).
Table 2 Effects of nutrient and water level in winter on survival rate and number of surviving plants of Eichhornia crassipes after winter (two-way ANOVA).
Figure 4 Plant number (A) and survival rate (B) (mean ± SD) of Eichhornia crassipes in different treatments after winter. Significant differences among the treatments are indicated by different letters at P < 0.05.
Discussion
In our study, both nutrients in the water and water level affected the survival rate of E. crassipes. E. crassipes originated in the tropics, and the low temperature in winter limits its distribution in introduced regions. Previous studies have shown that survival, growth, and clonal integration in E. crassipes are limited by low temperatures (Li et al., 1995, Wilson et al., 2005); therefore, increasing the temperature in winter can increase the survival rate of E. crassipes (You et al., 2013; Liu et al., 2016). In China, the Yangtze River basin occurs at the northern margin (32°N) of the distribution of E. crassipes. Although E. crassipes can grow and blossom in summer at higher latitudes, it cannot naturally survive in winter in China (Li and Xie, 2002). Similarly, E. crassipes also cannot overwinter successfully in the Laurentian Great Lakes, although it can grow and produce seed in the summer in this area (MacIsaac et al., 2016). The different treatments caused the stem bases of E. crassipes (overwintering organ) was exposed to different media, resulting them being subjected to different temperatures in winter. In our study, the covering of the stem bases with water can prevent direct damage from freezing and improve the overwintering temperature of the propagule. Therefore, the survival rate of E. crassipes in constant-water-level treatments was significantly higher. Previous studies also showed that water cover or sediment burial of stem bases facilitated the overwintering of E. crassipes (Owens and Madsen, 1995; You et al., 2013).
Similar to water cover, the litter layer can also buffer the cold temperatures and protected organisms under litter from freezing damage during winter and can therefore improve the survival rate of the organisms (Facelli and Pickett, 1991). Litter may also protect seedlings from being killed by frost in early spring (Heady, 1956). Previous studies have found that litter cover can improve the survival rates of animals and plants (Watt, 1970; Lahiri et al., 2015; Miura et al., 2017). In high-nutrient environments, E. crassipes plants are taller and larger and can form dense, interlocking mats. In winter, the large number of withered leaves can form a thick litter layer in high-nutrient treatments. In contrast, in the low-nutrient treatments, the litter layer was absent because of the low population density and the small and sparse leaves of E. crassipes. The water temperature was higher in the high-nutrient treatments than in the low-nutrient treatments because of the protection of the litter layer in winter. Moreover, the litter cover can also prevent the axillary buds away from the freezing damage.
The E. crassipes in the high-nutrient environment also developed a high-quality overwintering organ. In our study, the biomass, length, and diameter of the stem base in the high-nutrient treatments were all higher than those in the low-nutrient treatments. Meanwhile, the N concentration of the stem base was also higher in high-nutrient treatments than in the low-nutrient treatments. More storage leads to more protective substances to survive stressful environments. Plants with more vegetative storage proteins have been shown to increase in response to short days and low temperatures, improving their winter survival rates (Bertrand and Castonguay, 2003; Avice et al., 2003). Biomass and stem base size can also affect overwintering in E. crassipes. You et al. (2013) found that the overwintering survival rate of E. crassipes with large stem bases was much higher than that of plants with small stem bases. Although the starch concentrations of the stem base were similar in the high- and low-nutrient environments, the stem base in the high-nutrient environment still stored more starch, as the size of the stem base was larger. More carbohydrate reserves that make large stem bases are beneficial to the regrowth of new plants in the spring. Therefore, our study suggests that high levels of nutrients can improve the overwintering survival rate of E. crassipes in two ways: through the production of a thicker litter layer and the storage of more protective substances stored in the stem base.
The high nutrient level not only improved the overwintering survival rate of E. crassipes but also increased the performance of E. crassipes. In our experiments, the population density of E. crassipes in the eutrophic water increased to more than six times than that in the low-nutrient water. The individual biomass in the eutrophic water was 2.4 times that in the low-nutrient water. Our previous study found that, only at a high nutrient level, E. crassipes had a higher resource-use efficiency than the confamilial native aquatic plant Monochoria vaginalis (Fan et al., 2013). Zhao et al. (2006) also found that eutrophication further boosts the competitive advantages of water hyacinth over native plants and thus facilitates the invasion of this weed into water bodies. During the past 30 years in China, rapid urbanization, gross domestic product (GDP) increases, vast population growth, and living standard improvements have all produced domestic and industrial wastewater. Moreover, due to insufficient sewage treatment capacities, some of this wastewater is discharged, untreated, directly into rivers and lakes (Shao et al., 2006; Yang and Pang, 2006; Le et al., 2010), which causes organic pollution and eutrophication in many water bodies and the replacement of grass-dominated ecosystems with algae-dominated ecosystems (Jin et al., 2005). Seventy-three percent of the major lakes in China have undergone severe eutrophication, and the area of eutrophication amounts to 11,632 km2 (Li, 2006). Therefore, our results suggest that E. crassipes will spread to a wider area and cause worse effects under the background of intensified eutrophication and climate warming.
Many techniques have been used to control and eliminate the ecological and socio-economic impacts of E. crassipes (Villamagna and Murphy, 2010). Neochetina eichhorniae and Neochetina bruchi are two commonly used weevil species from the plant’s native range (Deloach and Cordo, 1976; Julien and Griffiths, 1999; Sosa et al., 2007). N. eichhorniae was introduced into China to control E. crassipes in 1995 (Ding et al., 2001). However, the population of N. eichhorniae was limited due to low temperatures in the Yangtze River basin. Our study indicated that eliminating eutrophication and regulating the water level can control or even eradicate E. crassipes in the Yangtze River basin. The overwintering survival rate of E. crassipes in the low-nutrient treatment was less than 5%, even all plants died in the low-nutrient and constant-water-level treatment. Musil and Breen (1977) also considered broad-scale nutrient reduction plans as the most sustainable solution for controlling E. crassipes outside of its native range. Even in water bodies with high nutrient levels, the overwintering survival rate of E. crassipes can be reduced by the water-drawdown treatment. Previous studies also found that drawdown can be used to manage aquatic vegetation (Nichols, 1975; Cooke, 1980).
In conclusion, our study found that high levels of nutrient not only increased the performance of E. crassipes but also improved the overwintering survival rate of E. crassipes by producing a thicker litter layer and more protective substances stored in the stem base in at the middle and lower reaches of the Yangtze River basin, which suggests that E. crassipes can invade higher latitudes under the trend of climate warming and water eutrophication, whereas exposing the stem base of E. crassipes to air of lower temperature by lowering the water level, which can reduce the survival rate of E. crassipes in winter. In addition, it also indicated that eliminating eutrophication and regulating the water level can control E. crassipes effectively in temperate regions and some subtropical regions.
Author Contributions
DY, SF, and CL designed the research and executed the research project. HY and XD collected the field data. SF and XD analyzed data. XD and HY wrote the paper.
Funding
This study was supported by the National Natural Science Foundation of China (31500295 and 31170339), the Major Science and Technology Program for Water Pollution Control and Treatment (2015ZX07503-005), and the Special Foundation of National Science and Technology Basic Research (2013FY112300).
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.
The handling editor is currently organizing a Research Topic with one of the authors CL, and confirms the absence of any other collaboration.
Acknowledgments
We thank Jing Li, Yuanyuan Gao, Ligong Wang, Shihe Li, Baobo Zhao, Yaozhou Fan, Shiliang Li, Lifu Cui and Changjun Cai for their valuable work in the experimental procedures and data collection.
References
Allen, M., Raper, S., Mitchell, J. (2001). Uncertainty in the IPCC’s third assessment report. Science 293, 430–433. doi: 10.1126/science.1062823
Arnell, N. W., Reynard, N. S. (1996). The effects of climate change due to global warming on river flows in Great Britain. J. Hydrol. 183, 397–424. doi: 10.1016/0022-1694(95)02950-8
Aurand, D. (1982). Nuisance aquatic plants and aquatic plant management programs in the United States, Vol 2, South Eastern Region. (McLean, VA: The Mitre Corporation).
Avice, J. C. L. D., Volenec, J. J. C. S., Castonguay, Y. (2003). Vegetative storage proteins in overwintering storage organs of forage legumes: roles and regulation. Can. J. Bot. 81, 1198–1212. doi: 10.1139/b03-122
Barrett, S. C. H. (1980). Sexual reproduction in Eichhornia crassipes (water hyacinth) II. Seed production in natural populations. J. Appl. Ecol. 17, 113–124. doi: 10.2307/2402967
Bertrand, A., Castonguay, Y. (2003). Plant adaptations to overwintering stresses and implications of climate change. Can. J. Bot. 81, 1145. doi: 10.1139/b03-129
Center, T. D. (1994). Biological control of weeds: water hyacinth and water lettuce. (Andover: Intercept).
Center, T. D., Spencer, N. R. (1981). The phenology and growth of water hyacinth (Eichhornia crassipes (Mart.) Solms) in a eutrophic Northcentral Florida Lake. Aquat. Bot. 10, 1–32. doi: 10.1016/0304-3770(81)90002-4
Chambers, P. A., Kalff, J. (1985). Depth distribution and biomass of submersed aquatic macrophyte communities in relation to Secchi depth. Can. J. Fish. Aquat. Sci. 42, 701–709. doi: 10.1139/f85-090
Charnov, E. L., Gillooly, J. F. (2003). Thermal time: body size, food quality and the 10°C rule. Evolution. Ecol. Res. 5, 43–51.
Chown, S. L., Huiskes, A. H. L., Gremmen, N. J. M. (2012). Continent-wide risk assessment for the establishment of nonindigenous species in Antarctica. Proc. Natl. Acad. Sci. U. S. A. 109, 4938–4943. doi: 10.1073/pnas.1119787109
Concilio, A. L., Loik, M. E., Belnap, J. (2013). Global change effects on Bromus tectorum L. (Poaceae) at its high-elevation range margin. Global Change Biol. 19, 161–172. doi: 10.1111/gcb.12032
Cooke, G. D. (1980). Lake level drawdown as a macrophyte control technique. J. Am. Water Resour. Assoc. 16, 317–322. doi: 10.1111/j.1752-1688.1980.tb02397.x
Deegan, B. M., White, S. D., Ganf, G. G. (2006). The influence of water level fluctuations on the growth of four emergent macrophyte species. Aquat. Bot. 86, 309–315. doi: 10.1016/j.aquabot.2006.11.006
Deloach, C. J., Cordo, H. A. (1976). Life cycle and biology of Neochetina bruchi, a weevil attacking water hyacinth in Argentina, with notes on N. eichhorniae. Annals Entomol. Soc. Am. 69, 643– 652. doi: 10.1093/aesa/69.4.643
Ding, J. Q., Chen, Z. Q., Fu, W. D., Wang, R., Zhang, G. L., Lu, X. J., et al. (2001). Control Eichhornia crassipes, an invasive aquatic weed in South China with Neochetina eichhorniae. Chin. J. Biol. Control 17 (3), 97–100. doi: 10.16409/j.cnki.2095-039x.2001.03.001
Facelli, J. M., Pickett, S. T. (1991). Plant litter: its dynamics and effects on plant community structure. Bot. Rev. 57 (1), 1–32. doi: 10.1007/BF02858763
Fan, S., Liu, C., Yu, D., Xie, D. (2013). Differences in leaf nitrogen content, photosynthesis, and resource-use efficiency between Eichhornia crassipes and a native plant Monochoria vaginalis in response to altered sediment nutrient levels. Hydrobiologia 711, 129–137. doi: 10.1007/s10750-013-1471-3
François, J. 1969. Recherches experimentales sur l’ecologie de la jacinthe d’eau (Eichhornia crassipes (Mart.) Solms).
Freidel, J. W., Koch, W., Philipp, O. (1978). Untersuchungen zur Biologie und Populations dynamik von Eichhornia crassipes (Mart.) Solms. in Sudan. Paper presented at 5th EWRS international symposium of aquatic weeds, Amsterdam, 4-8 Sept 1978.
Gao, L. (2005). Nutrient control of clonal growth of invasive Eichhornia crassipes, and its spatiotemporal distribution pattern in Shanghai. Ph.D. thesis, Fudan University.
Hansen, J., Moller, I. B. (1975). Percolation of starch and soluble carbohydrates from plant tissue for quantitative determination with anthrone. Anal. biochemi. 68 (1), 87–94. doi: 10.1016/0003-2697(75)90682-X
Heady, H. F. (1956). Changes in the central California annual plant community induced by the manipulation of natural mulch. Ecology 37, 798–811. doi: 10.2307/1933071
Hellmann, J. J., Byers, J. E., Bierwagen, B. G., Dukes, J. S. (2008). Five potential consequences of climate change for invasive species. Conserv. Biol. 22 (3), 534–543. doi: 10.1111/j.1523-1739.2008.00951.x
Ishii, J., Kadono, Y. (2004). Sexual reproduction under fluctuating water levels in an amphibious plant Schoenoplectus lineolatus (Cyperaceae): a waiting strategy? Limnology 5, 1–6. doi: 10.1007/s10201-003-0108-z
Jin, X., Xu, Q., Huang, C. (2005). Current status and future tendency of lake eutrophication in China. Sci. Chin. 48, 948–954. doi: 10.1360/062005-286
Julien, M. H., Griffiths, M. W. (1999). Biological Control of Weeds, A world catalogue of agents and their target weeds. 4th ed. Wallingford, U K: CAB International, 223.
Lahiri, S., Orr, D., Sorenson, C., Cardoza, Y. (2015). Overwintering refuge sites for Megacopta cribraria (Hemiptera: Plataspidae). J. Entomol. Sci. 50 (1), 69–73. doi: 10.18474/0749-8004-50.1.69
Le, C., Zha, Y., Li, Y., Sun, D., Lu, H., Yin, B. (2010). Eutrophication of lake waters in China: cost, causes, and control. Environ. Manage. 45, 662–668. doi: 10.1007/s00267-010-9440-3
Li, S. J. (2006). An approach to accelerating innovative development of the lake science. Bull. Chin. Acad. Sci 21 (5), 399–405. doi: 10.16418/j.issn.1000-3045.2006.05.014
Li, X. B., Wu, Z. B., He, G. Y. (1995). Effects of low temperature and physiological age on superoxide dismutase in water hyacinth (Eichhornia crassipes Solms). Aquat. Bot. 50, 193–200. doi: 10.1016/0304-3770(94)00417-K
Li, Z. Y., Xie, Y. (2002). Invasive alien species in China. (Beijing: China Forestry Publishing House).
Liu, J., Chen, X., Wang, Y., Li, X., Yu, D., Liu, C. (2016). Response differences of Eichhornia crassipes to shallow submergence and drawdown with an experimental warming in winter. Aquat. Ecol. 50 (2), 307–314. doi: 10.1007/s10452-016-9579-y
MacIsaac, H. J., Eyraud, A. P., Beric, B., Ghabooli, S. (2016). Can tropical macrophytes establish in the Laurentian Great Lakes? Hydrobiologia 767 (1), 165–174. doi: 10.1007/s10750-015-2491-y
Madsen, J. D., Luu, K. T., Getsinger, K. D. (1993). Allocation of biomass and carbohydrates in water hyacinth (Eichhornia crassipes): pond-scale verification. Technical Report A93-3. Vicksburg, MS: US Army Corps of Engineers, Waterways Experiment Station. doi: 10.21236/ADA261931
Merow, C., Bois, S. T., Allen, J. M., Xie, Y., Silander, J. A. (2017). Climate change both facilitates and inhibits invasive plant ranges in New England. Proc. Natl. Acad. Sci. 114 (16), E3276–E3284. doi: 10.1073/pnas.1609633114
Mitchell, D. S. (1985). “Surface-floating aquatic macrophytes,” in The ecology and management of African wetland vegetation. Ed. Denny, P. (Dordrecht: Dr. W. Junk Publishers), 109–124. doi: 10.1007/978-94-009-5504-2_4
Miura, K., Watanabe, N., Negishi, J. N. (2017). Leaf litter patches in stream create overwintering habitats for Ezo brown frog (Rana pirica). Limnology 18 (1), 9–16. doi: 10.1007/s10201-016-0491-x
Musil, C. F., Breen, C. M. (1977). The application of growth kinetics to the control of Eichhornia crassipes (Mart) Solms. through nutrient removal by mechanical harvesting. Hydrobiologia 53 (2), 165–171. doi: 10.1007/BF00029295
Nichols, S. A. (1975). The use of overwinter draw down for aquatic vegetation management. J. Am. Water Resour. Assoc. 11, 1137–1148. doi: 10.1111/j.1752-1688.1975.tb01837.x
Oki, Y. 1984. Response of water hyacinth to low temperature. Paper presented at international conference on water hyacinth, India, Feb 1984.
Oki, Y., Ueki, K. (1984). Adaptation of water hyacinth grown under various habitats. Paper presented at Proceedings of the International Conference on Water Hyacinth; Hyderabad, India.
Owens, C. S., Madsen, J. D. (1995). Low temperature limits of water hyacinth. J. Aquat. Plant. Manag. 33, 63–68.
Owens, C. S., Smart, R. M., Stewart, R. M. (2004). Low temperature limits of giant salvinia. J. Aquat. Plant. Manag. 42, 91–94.
Rahel, F. J., Olden, J. D. (2008). Assessing the effects of climate change on aquatic invasive species. Conserv. Biol. 22 (3), 521–533. doi: 10.1111/j.1523-1739.2008.00950.x
Reddy, K. R., Agami, M., Tucker, J. C. (1989). Influence of nitrogen supply rates on growth and nutrient storage by water hyacinth (Eichhornia crassipes) plants. Aquat. Bot. 36 (1), 33–43.215. doi: 10.1016/0304-3770(89)90089-2
Reddy, K. R., Agami, M., Tucker, J. C. (1990). Influence of phosphorus on growth and nutrient storage by water hyacinth (Eichhornia crassipes (Mart.) Solms) plants. Aquat. Bot. 37 (4), 355–365. doi: 10.1016/0304-3770(90)90021-C
Ripley, B. S., Muller, E., Behenna, M., Whittington-Jones, G. M., Hill, M. P. (2006). Biomass and photosynthetic productivity of water hyacinth (Eichhornia crassipes) as affected by nutrient supply and mirid (Eccritotarus catarinensis) biocontrol. Biol. Control 39 (3), 392–400. doi: 10.1016/j.biocontrol.2006.05.002
Rodríguez-Gallego, L., Mazzeo, N., Gorga, J., Meerhoff, M., Clemente, J., Kruk, C., et al. (2004). Effects of an artificial wetland of free-floating plants on the restoration of a hypertrophic subtropical lakes. Lakes Reservoirs Res. Manage. 9, 203–215. doi: 10.1111/j.1440-1770.2004.00245.x
Ryther, J. H., Dunstan, W. M. (1971). Nitrogen, phosphorus, and eutrophication in the coastal marine environment. Science 171 (3975), 1008–1013. doi: 10.1126/science.171.3975.1008
Schindler, D. W. (2006). Recent advances in the understanding and management of eutrophication. Limnol. Oceanography 51 (1part2), 356–363. doi: 10.4319/lo.2006.51.1_part_2.0356
Shao, M., Tang, X., Zhang, Y., Li, W. (2006). City clusters in China: air and surface water pollution. Front. Ecol. Environ. 4, 353–361. doi: 10.1890/1540-9295(2006)004[0353:CCICAA]2.0.CO;2
Smith, R. G. B., Brock, M. A. (2007). The ups and downs of life on the edge: the influence of water level fluctuations on biomass allocation in two contrasting aquatic plants. Plant Ecol. 188, 103–116. doi: 10.1007/s11258-006-9151-2
Smith, V. H., Tilman, G. D., Nekola, J. C. (1999). Eutrophication: impacts of excess nutrient inputs on freshwater, marine, and terrestrial ecosystems. Environ. Pollut. 100 (1-3), 179–196. doi: 10.1016/S0269-7491(99)00091-3
Sorte, C. J., Ibáñez, I., Blumenthal, D. M., Molinari, N. A., Miller, L. P., Grosholz, E. D., et al. (2013). Poised to prosper? A cross-system comparison of climate change effects on native and non-native species performance. Ecology Lett. 16 (2), 261–270. doi: 10.1111/ele.12017
Sosa, A. J., Cordo, H. A., Sacco, J. (2007). Preliminary evaluation of Megamelus scutellaris Berg (Hemiptera: Delphacidae), a candidate for biological control of water hyacinth. Biol. Control 42, 129–138. doi: 10.1016/j.biocontrol.2007.04.012
Téllez, T. R., López, E. M. D. R., Granado, G. L., Pérez, E. A., López, R. M., Guzmán, J. M. S. (2008). The water hyacinth, Eichhornia crassipes: an invasive plant in the Guadiana River Basin (Spain). Aquat. Invasions 3 (1), 42–53. doi: 10.3391/ai.2008.3.1.8
Tyndall, R. W. (1982). Nuisance aquatic plants and aquatic plant management programs in the United States, Vol 1, Southwestern Region. McLean, VA: The Mitre Corporation.
Ueki, K., Ito, M., Oki, Y. (1976). Water hyacinth and its habitats in Japan. Paper presented at 5th Asian-Pacific Weed Science Society Conference, Tokyo.
Villamagna, A. M., Murphy, B. R. (2010). Ecological and socio-economic impacts of invasive water hyacinth (Eichhornia crassipes): a review. Freshwater Biol. 55 (2), 282–298. doi: 10.1111/j.1365-2427.2009.02294.x
Walther, G. R., Post, E., Convey, P., Menzel, A., Parmesan, C., Beebee, T. J., et al. (2002). Ecological responses to recent climate change. Nature 416 (6879), 389. doi: 10.1038/416389a
Walther, G. R., Roques, A., Hulme, P. E., Sykes, M. T., Pyšek, P., Kühn, I., et al. (2009). Alien species in a warmer world: risks and opportunities. Trends Ecol. Evol. 24 (12), 686–693. doi: 10.1016/j.tree.2009.06.008
Watt, A. S. (1970). Contribution to the ecology of bracken (Pteridium aquilinum). VII. Bracken and litter. 3. The cycle of change. New Phytol. 69, 431–449. doi: 10.1111/j.1469-8137.1970.tb02442.x
Williamson, M., Fitter, A. (1996a). The varying success of invaders. Ecology 77 (6), 1661–1666. doi: 10.2307/2265769
Williamson, M. H., Fitter, A. (1996b). The characters of successful invaders. Biol. Conserv. 78 (1-2), 163–170. doi: 10.1016/0006-3207(96)00025-0
Wilson, J. R., Holst, N., Rees, M. (2005). Determinants and patterns of population growth in water hyacinth. Aquat. Bot. 81, 51–67. doi: 10.1016/j.aquabot.2004.11.002
Woodward, F. I. (1987). Climate and plant distribution. (Cambridge, UK, New York, NY, USA: Cambridge University Press).
Xiao, K. Y., Yu, D., Wu, Z. H. (2007). Differential effects of water depth and sediment type on clonal growth of the submersed macrophyte Vallisneria natans. Hydrobiologia 589, 265–272. doi: 10.1007/s10750-007-0740-4
Xie, D., Yu, D., Yu, L. F., Liu, C. H. (2010). Asexual propagations of introduced exotic macrophytes Elodea nuttallii, Myriophyllum aquaticum, and M. propinquum are improved by nutrient-rich sediments in China. Hydrobiologia 655 (1), 37–47. doi: 10.1007/s10750-010-0402-9
Xie, Y., Luo, W., Wang, K., Ren, B. (2008). Root growth dynamics of Deyeuxia angustifolia seedlings in response to water level. Aquat. Bot. 89, 292–296. doi: 10.1016/j.aquabot.2008.03.003
Xie, Y., Wen, M., Yu, D., Li, Y. (2004). Growth and resource allocation of water hyacinth as affected by gradually increasing nutrient concentrations. Aquat. Bot. 79 (3), 257–266. doi: 10.1016/j.aquabot.2004.04.002
Yang, X., Pang, J. (2006). Implementing China’s “Water Agenda 21”. Front. Ecol. Environ. 4, 362–368. doi: 10.1890/1540-9295(2006)004[0362:ICWA]2.0.CO;2
You, W., Yu, D., Xie, D., Yu, L. (2013). Overwintering survival and regrowth of the invasive plant Eichhornia crassipes are enhanced by experimental warming in winter. Aquat. Biol. 19 (1), 45–53. doi: 10.3354/ab00519
Keywords: eutrophication, water drawdown, invasion, overwintering, Eichhornia crassipes
Citation: Yu H, Dong X, Yu D, Liu C and Fan S (2019) Effects of Eutrophication and Different Water Levels on Overwintering of Eichhornia crassipes at the Northern Margin of Its Distribution in China. Front. Plant Sci. 10:1261. doi: 10.3389/fpls.2019.01261
Received: 29 July 2018; Accepted: 11 September 2019;
Published: 04 October 2019.
Edited by:
Katya E. Kovalenko, University of Minnesota Duluth, United StatesReviewed by:
Thaísa Sala Michelan, Federal University of Pará, BrazilWei Xing, Chinese Academy of Sciences, China
Copyright © 2019 Yu, Dong, Yu, Liu and Fan. 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: Shufeng Fan, ZmFucmFuOTExQDE2My5jb20=
†These authors have contributed equally to this work