Introduction

Wetland is key habitat that regulates flow of nutrients between landscape and atmosphere because of their existence at the interface between terrestrial and aquatic zones. Wetlands are highly dynamic ecosystems in terms of hydrology and recycling of nitrogen, and considered as one of the most invaded habitats worldwide1. Hydrological turbulence is a common stress for plants in wetland ecosystems and it inevitably imposes stress on plant communities and affects the performance of plants in various transitional terrestrial and amphibious eco-systems2,3. Hydrological variations within wetland often determine the pattern of plant zonation and community structure. The regime of water at wetland is characterized by the depth, length and frequency of flood4,5.

The fluctuations of water at different depths in the wetland ecosystem disturb the community of native species and that disturbance facilitates the primary mechanism involved in plant invasions by removing the native species6. Simultaneous fluctuations in water and nutrient levels will affect the phenotypic plasticity and interspecific interactions among invasive and native species. High phenotypic plasticity and competitive ability are key factors of successful invasion for invasive species7,8,9. Higher phenotypic plasticity enhances adaptability of invasive species in response to changes in environment at wetlands10. Nevertheless, the competitive ability of invasive and native species varies with water availability and it may be altered by environmental variations11,12. These functional traits are involved directly or indirectly in the mechanism of successful plant invasion of invasive species over their co-occurring native species that experience the similar environmental selective pressures13.

Moreover, functional traits of plants that are associated with their response to environmental changes have also been central theme for predicting the fitness of plants and help plants to cope to different environmental habitats14,15. Several studies have shown that certain plants successfully invade certain environments because of higher specific leaf area (SLA). Higher SLA can enable invasive species to acquire more resources and grow at a high growth rate than co-occurring native species16,17. It has also been documented in numerous studies that invasive species gain competitive advantages over co-occurring native species in introduced range through increasing SLA and leaf nutrients such as leaf nitrogen (Ln)18,19. Leaf nitrogen (Ln) is the most essential component for a plant, linked with higher SLA, net photosynthetic rates and photosynthetic nitrogen use efficiency and contributing to higher production of biomass13,20,21,22,23. One preceding study, Chen, et al.24 noted that invasive Alternanthera philoxeroides (Mart.) Griseb showed higher photosynthetic capacity, and produced more biomass in deep submergence. Hussner, et al.25 reported that shoot biomass, root biomass and total biomass of Myriophyllum aquaticum (vell.) Verdic were increased with increasing nutrient availability at different water levels. There are also some other conflicting views about the wetland plants that their photosynthetic and growth properties were mainly affected by availability of water at varied depth with different nutrient levels26,27,28. However, with our scope, no reports have dealt with how an invasive species and its native competitors respond to water fluctuations at different depth along with nutrient concentration levels in wetlands.

Therefore, based on the responses of different functional traits to different environments, we took a successful invader Wedelia trilobata (L.) Hitchc. (Asteraceae) and its congener, native Wedelia chinensis (Osbeck.) Merr for our studies. W. trilobata is consider as native species in the tropical region of South America29,30, and is found as the world’s most harmful clonal evergreen creeping invasive species31. In early 1970, W. trilobata was also found on a large-scale in southern region of China32. In China, initially it was spread rapidly from grounds to roadsides and then to agricultural fields33,34. W. trilobata has an ability to survive in every habitat condition. It can bear nutrient and water variations but it prefers to grow in nutrient rich environment with high amount of water35. While, W. chinensis is the native congener of W. trilobata, mostly used as medicinal plant. W. chinensis grow slowly as compared to growth rate of W. trilobata35,36. Since, China is among the world 10-mega biodiversity countries that play a leading role in ensuring the safety of food and agricultural production. According to environmental variation in different region it is necessary to predict the future expansion of invasive species such as W. trilobata in wetland ecosystem. With the above mentioned shortfall regarding the behavior of invasive W. trilobata in wetlands, we hypothesized that 1) W. trilobata will show better responses of their functional traits under water fluctuations at different depth than its native congener W. chinensis under both mono and mixed culture. 2) highly-fluctuated water depth along with high nutrient concentrations will facilitate the W. trilobata and make it successful invader over W. chinensis in mixed culture. This study is linked with different functional traits under different environmental conditions at wetland and, could be helpful to identify the most dominant factors that help invasive plants to become more invasive. Ultimately, the information generated through this study will help in devising the management tools to stop further expansion of this invasive plant species.

Results

Biomass, leaf area and specific leaf area

Water depth (WD), nutrient levels (N) and species (S) under both mono and mixed culture significantly affected the AGBm, BGBm, LA and SLA of invasive W. trilobata and its native W. chinensis (Table 1). In case of AGBm, WD, N and S had dignificant results (P < 0.001) but the interaction WD*N, WD*S and N*S were noted non-significant (P > 0.05). The interaction WD*N*S between all of them had also non-significant results on AGBm (P > 0.05). Consequently, for BGBm the interaction WD*N, N*S, and interaction between all of them (WD*N*S) had also non-significant results (P > 0.05). However, the results were noted significant for the interaction between WD and S (P < 0.01). For LA and SLA, the differences were noted significant (P < 0.01, P < 0.001) for all the interaction.

Table 1 ANOVA results with interactions among water depth, nutrients levels and species for the effects of water depth fluctuations with different nutrients treatments on competition, physiology and growth related data for W. trilobata and W. chinensis.
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Water depth up to 15 cm along with low nutrient concentration (from n1 to n3) affected AGBm, BGBm, LA and SLA of W. chinensis under both mono and mixed culture, (Figs. 1 and 2). W. trilobata produced more biomass and had higher values of AGBm and BGBm at low water depth levels i.e. 5 cm static water depth (5S) and 5 cm fluctuated water depth (5F) with all levels of nutrient concentrations i.e. n1, n2, n3 in mono culture as well as in mixed culture (Fig. 1). The fluctuated water depth (15F) at 15 cm along with nutrient concentrations levels of n1 and n2 under mixed culture, exhibited significant positive effect on W. trilobata and W. trilobata showed significantly higher values of LA and SLA, respectively than W. chinensis (Table 1; Fig. 2). However under mixed culture, water depth at 15 cm along with low nutrient concentration at n3 affect the AGBm, BGBm, LA and SLA of W. trilobata but it did not affect the AGBm, BGBm, LA and SLA of W. trilobata at 5 cm static water depth under both mono and mixed culture (Figs. 1 and 2).

Figure 1
figure 1

Effects of water depth fluctuations with different nutrient treatments on the (a) above ground biomass in mono culture, (b) above ground biomass in mixed culture, (c) below ground biomass in mono culture, (d) below ground biomass in mixed culture of W. trilobata and W. chinensis. Dominating above ground and below ground biomass of W. trilobata (white bars) over W. chinensis (red bars) are denoted by mean + SE with different letters which indicated a significant difference of nitrogen and water depth treatments among mono and mixed culture (at P < 0.05). Note: ABGm is above ground biomass; BGBm is below ground biomass; WC is W. chinensis; WT is W. trilobata; MIXWC is W. chinensis in mixed culture; and MIXWT is W. trilobata in mixed culture.

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Figure 2
figure 2

Effects of water depth fluctuations with different nutrient treatments on the (a) leaf area in mono culture, (b) leaf area in mixed culture, (c) specific leaf area in mono culture, (d) specific leaf area in mixed culture of W. trilobata and W. chinensis. Dominating leaf area and specific leaf area of W. trilobata (white bars) over W. chinensis (red bars) are denoted by mean + SE with different letters indicate a significant difference of nitrogen and water depth treatments among mono and mixed culture (at P < 0.05). Note: ABGm is above ground biomass; BGBm is below ground biomas; WC is W. chinensis; WT is W. trilobata; MIXWC is W. chinensis in mixed culture; and MIXWT is W. trilobata in mixed culture.

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Relative competition and plasticity index

The obtained results from the measurement exhibited the significant effect on the RCI and PI. The differences were noted highly significant (P < 0.001) for RCI in water depth, nutrients and species and were noted significant (P < 0.01) in the interaction among water depth, nutrients, species and their interaction (Table 1).

The average values of RCI for W. trilobata were positive when grown at the 5 cm water depth with low and high nutrient concentrations either the condition was static or fluctuated and were negative at the 15 cm water depth with low and high nutrient concentrations except at 15 cm fluctuated water depth with control nutrient concentration (15Fn1) (Table 1; Fig. 3). The mean values for W. chinensis were decreased with the increasing water depth and fluctuation; the value in the 15Sn3 treatment was more negative and indicated sensitivity of the W. chinensis in mixed planting than its competitor W. trilobata (Fig. 3).

Figure 3
figure 3

Effects of water depth fluctuations with different nutrient treatments on the relative competition index in mixed culture of W. trilobata and W. chinensis. Positive values of relative competition index of W. trilobata (white bars) over W. chinensis (red bars) are denoted by mean + SE with different letters indicate a significant difference of nitrogen and water depth treatments among mono and mixed culture (at P < 0.05). Note: RCI is relative competition index; WC is W. chinensis; WT is W. trilobata.

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The values of PI for W. trilobata were higher than its native congener W. chinensis in favorable and unfavorable conditions of water depth and nutrient fluctuations (Fig. 4). The PI was significantly higher for W. trilobata in all growth (AGBm, BGBm, LA and SLA) and physiological traits (Pn, Ln, PNUE), respectively as compared to W. chinensis under both mono and mixed culture. W. chinensis showed no plasticity (close to zero) under mixed planting and it was noted 0.020, 0.080, 0.003, 0.010, 0.007, 0.100, and 0.060 for Pn, Ln, PNUE, LA, SLA, AGBm and BGBm, respectively (Fig. 4).

Figure 4
figure 4

Effects of water depth fluctuations with different nutrient treatments on the plasticity index in mixed culture of W. trilobata and W. chinensis. Mean + SE with different letters indicate a significant difference of nitrogen and water depth treatments on plasticity index by considering different functional traits among mono and mixed culture treatments (at P < 0.05). Note: Pn is net photosynthetic rate; Ln is leaf nitrogen; PNUE is photosynthetic nitrogen use efficiency; LA is leaf area, SLA is specific leaf area; ABGm is above ground biomass; BGBm is below ground biomas WC is W. chinensis; WT is W. trilobata; MIXWC is W. chinensis in mixed culture; and MIXWT is W. trilobata in mixed culture.

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Net photosynthetic rate, leaf nitrogen and photosynthetic nitrogen use efficiency

In mono and mixed culture, ANOVA result showed the significant and non-significant differences among all the treatments, species and their interactions for Pn, Ln and PNUE (Table 1). The effect of water depth and nutrient concentration on Pn, Ln and PNUE was noted significant (P < 0.001). However, when considering the interaction among all factors (water depth × nutrients; water depth × species; nutrient × species; water depth × nutrient × species), the results noted for Pn were non-significant (P > 0.05), but the results was noted significant (P < 0.01, P < 0.001) for Ln and PNUE (Table 1). Physiological responses including Pn, Ln and PNUE were significantly lower in native W. chinensis under both mono and mixed culture than in its invasive congener W. trilobata (Table 1; Figs. 5 and 6).

Figure 5
figure 5

Effects of water depth fluctuations with different nutrient treatments on the (a) photosynthetic rate in mono culture (b) photosynthetic rate in mixed culture, (c) leaf nitrogen in mono culture, (d) leaf nitrogen in mixed culture of W. trilobata and W. chinensis. Dominating photosynthetic rate and leaf nitrogen of W. trilobata (white bars) over W. chinensis (red bars) are denoted by mean + SE with different letters indicate a significant difference of nitrogen and water depth treatments among mono and mixed culture (at P < 0.05). Note: Pn is net photosynthetic rate; Ln is leaf nitrogen; WC is W. chinensis; WT is W. trilobata; MIXWC is W. chinensis in mixed culture; and MIXWT is W. trilobata in mixed culture.

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Figure 6
figure 6

Effects of water depth fluctuations with different nutrient treatments on the (a) photosynthetic nitrogen use efficiency in mono culture, (b) photosynthetic nitrogen use efficiency in mixed culture of W. trilobata and W. chinensis. Dominating photosynthetic nitrogen use efficiency of W. trilobata (white bars) over W. chinensis (red bars) are denoted by Mean + SE with different letters indicate a significant difference of nitrogen and water depth treatments among mono and mixed culture (at P < 0.05). Note: PNUE is photosynthetic nitrogen use efficiency; WC is W. chinensis; WT is W. trilobata; MIXWC is W. chinensis in mixed culture; and MIXWT is W. trilobata in mixed culture.

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Generally, the Pn and Ln of both W. trilobata and W. chinensis decreased with increasing water depth and by lowering the nutrients concentrations but Pn and Ln of W. chinensis were more affected at high water depth of 15S with very low level of nutrients (n3) under both mono and mixed culture, respectively. Consequently, the values of Pn ranging from 2.35 to 8.16 μmol (CO2) m−2 s−1 were recorded for W. trilobata in mono culture, while the values of Pn ranging from 1.83 to 7.55 μmol (CO2) m−2 s−1 were noted in the mixed culture, respectively. However, for W. chinensis, the values of Pn ranged from 1.37 to 7.68 μmol (CO2) m−2 s−1 in mono culture and 1.26 to 6.40 μmol (CO2) m−2 s−1 in mixed culture, respectively (Fig. 5). Upon treatments, in case of W. trilobata, a substantial increase in PNUE 10.68 μmol g−1 s−1 and 7.67 μmol g−1 s−1 was observed at 15Sn2 and 15Sn3 (15S static water depth with low concentration of nutrients n2 and n3) under both mono and mixed culture, respectively (Fig. 6). On the other hand, W. chinensis showed reduction in the values of PNUE for all nutrient concentrations under both mono and mixed culture (Fig. 6). Overall, W. chinensis was found more sensitive than its competitor W. trilobata under mixed culture (Figs. 5 and 6).

Discussion

Generally, plants suffer from oxygen deficiency during hydrological fluctuations at wetland, resultantly plant growth is affected37,38. However, the hydrological fluctuations such as change in water depth along with high nutrient concentrations did not affect the growth of invasive W. trilobata in both cultur (mono and mixed) (Table 1). In some proceeding studies related to wetland plants, it has been noted that some plants can stand and grow well at water depth fluctuation up to 30 cm and produce high biomass28,39. Luo, et al.40 explained that plant’s growth did not affect byslight fluctuations in water depth in wetlands. In our study, the fluctuation in water depth up to 5 cm was low range to affect the growth rate of both invasive W. trilobata and native W. chinensis (Fig. 1). The above description about the behavior of invasive W. trilobata and native species W. chinensis is supported as may be that both species have an ability to tolerate such small water depth fluctuations and showed compensatory growth. The fluctuations of water depth along with different nutrients concentration could also influence the growth of the target plants41,42. In literature, it was recorded that increasing nutrients concentrations supported the growth of invasive Alternanthera philoxeroides under high submergence and alleviated its negative effect43. In the following study, LA and SLA of the W. chinensis decreased with increasing water depth along with low nutrients, and inhibited the growth of the W. chinensis (Fig. 2). However, increased water depth along with high nutrient concentrations added more biomass (allocated to shoot and root) in form of AGBm and BGBm in W. trilobata, supportive by the results of Zhang et al.43 that massive allocated stem biomass found benefited for invasive Alternanthera philoxeroides under submergence. Similarly in our study, W. trilobata increased its AGBm under high fluctuated water depth along with high nutrient concentrations, which could increase the O2, CO2 and light uptake, and found helpful for W. trilobata to promote its growth.

It has been suggested in several studies that invasive species invest more biomass in the development of leaf to obtain a high growth rate16,44. Meanwhile, high SLA is correlated with the growth development of plants and it was expected that SLA of invasive species would be higher than the native species13. The results of this study exhibited that the SLA of invasive W. trilobata was significantly higher in all water depths than the native W. chinensis (Fig. 2). This indicated that W. trilobata has relatively higher growth rate and have more ability to utilize resources than native W. chinensis. However, high reduction in the growth traits and higher consumption of carbohydrates during limited available nutrients in deep submergence might decrease the tolerance of W. chinensis and make it sensitive.

The growth inhibition of plants may not be caused only by stress due to submergence but there are also other plant traits like interspecific interactions and intraspecific interactions, that can be exaggerated by the hydrological variation in the wetland ecosystem45. Relative competition index of W. trilobata and W. chinensis was significantly affected by fluctuation of water depth along with different treatments (Table 1; Fig. 3). W. trilobata benefited more and perform better during relative competitive under mixed_culture over its native congener W. chinensis because during suitable environment, W. trilobata showed better competition and in a stressful environment W. trilobata exhibit more facilitation. It seemed that, there is a trade-off noted among plants between facilitation and competition, as it was explained in the study did by Zhou et al.46 about trade-off of plants during interaction. Moreover, every plant species have different tolerance levels and survival rate to the worse environmental conditions, and here W. trilobata seems to be better capable to utilize the resources under high fluctuation of water depths along with decreased nutrients concentrations at 15 cm because of its better relative competition and phenotypic plasticity.

Phenotypic plasticity is the potential target for researchers to confer the fitness advantage of invasive plants in their habitats47,48 and it may play a little-understood role in the successful invasion13. This study examined all functional traits (Pn, Ln, PNUE, LA, SLA, and biomass) of the both the studied species to display the phenotypic plasticity as plasticity index (Fig. 4). These functional traits may present the certain extent of phenotypic plasticity, which may be influenced by the adaptation of plants in the poor resource environment. Therefore, the PI in all functional traits of W. trilobata was higher than the PI of its native W. chinensis under both mono and mixed culture (Fig. 4). However, higher PI of W. trilobata over W. chinensis may enable them to gain advantage in high water depth with low nutrients and increase its resource use efficiency. Moreover, previous studies investigative the interaction between phenotypic plasticity and plant invasion and found that invasive species showed higher plasticity over native species, and higher plasticity was considered as the main driver in successful invasion10,49.

W. trilobata also showed higher values of photosynthetic rate over its native congener W. chinensis under both mono and mixed cultures (Table 1, Figs. 5 and 6). As higher photosynthetic rate of invasive species may contribute to the higher production of biomass and support its relative growth rate even in the nutrient poor habitat50,51,52,53. The higher Pn of the invasive W. trilobata may be associated with their nutrient use efficiency to the photosynthetic machinery, indicated by the PNUE (Fig. 6). Funk, et al.54 noted that invasive species have significantly higher PNUE and photosynthetic energy use efficiency than their co-occurring native species in low nutrient environment. It was also noted the higher PNUE for invasive Eupatorium adenophorum than its two native congeners55. Thus, we have found that the higher PNUE may contribute to higher Pn for the invasive W. trilobata, and sustain their photosynthetic rate in high water depth with nutrient deficit conditions. This indicated that W. trilobata possess high resource capture ability, supporting our hypothesis by signifying that these traits may play a little-understood role in the successful invasion of W. trilobata in wetland eco-system (Fig. 7).

Figure 7
figure 7

Schematic representation about the summary of the following research as functional traits facilitate the W. trilobata over its native W. chinensis.

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In the present study, we have found that W. trilobata had higher photosynthetic rate, photosynthetic nutrient use efficiency, relative competition index and plasticity index than the co-occurring native W. chinensis. W. trilobata adopted a conservative resource use strategy in order to sustain in high fluctuation of water depth with nutrient poor environment. In contrast, W. chinensis presented lower values of functional traits, and showed sensitivity because of its lower plasticity and lower relative competitive ability to high fluctuation of water depth under mixed culture. Here, native W. chinensis might be inhibited under mixed culture by two factors; one its competition with invasive W. trilobata and second its sensitivity to high water depth fluctuation with nutrient deficiency. While, high nutrients (n1) under high water depth promoted the growth of invasive W. trilobata and led to survive in such condition, which may partially describe the ability of W. trilobata to invade waterlogged wetland habitats. As high N supports invasiveness of the invasive species; hence avoid addition of nutrients to water bodies. Moreover, our results also helpful to understand the dynamics of species in relation to flooding in wetlands.

Figure 8
figure 8

Schematic representation of the four water depth variations. 5S, static water level at 5 cm; 5F, water depth fluctuating from 5 cm with a 10 cm amplitude; 15S, static water level at 15 cm; 15F, water depth fluctuating from 15 cm with a 10 cm amplitude. The shaded blue areas indicate the static water depth, and green and red shaded areas indicate the fluctuations.

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Materials and Methods

Plant material, treatments and experimental design

The experiment was conducted at Jiangsu University, under greenhouse conditions. The greenhouse had natural lighting with (25/18) ± 2 °C (day/night) temperature and 70% relative humidity. The ramets of W. trilobata and W. chinensis were collected from the single location (32.20°N, 119.45°E) of Jiangsu University, Zhenjiang, Jiangsu, P. R. China in 3rd March, 2019. About 900 ramets collected for both species and then cultured in a sand medium in a seedling tray. These seedlings irrigated daily with tapwater in order to adapt the greenhouse conditions. On 20th March, 720 ramets of both species (360 for each) were selected to conduct the following experiment. The plants were divided into two groups as mono-culture and mixed culture. Plants of both species were planted in mono (2: 0, 0: 2) and mixed- culture (1: 1) in an internal pot (diameter: 18 cm × height: 12 cm). These pots were filled with clean washed sand and then placed to an outer pots (diameter: 28 cm × height: 35 cm).

In order to simulate the naturally occurring water fluctuations at different depth in wetlands, plants were subjected to three nutrient concentration levels of Hoagland solution crossed with four different water depths on 25th April. For water depth fluctuations, four treatments levels were established according to Sun et al.56 and Zhou et al.28: (1) static-water level at 5 cm, coded as 5S; (2) fluctuated-water level at 5 cm, fluctuating between 5 and 10 cm water depth, coded as 5F; (3) static-water level at 15 cm, coded as 15S; and (4) fluctuated-water level at 15 cm, fluctuating between 15 and 25 cm water depth, coded as 15F (Fig. 8). The nutrients concentration applied as full-strength Hoagland solution (n1), 1/4-strength Hoagland solution (n2) and 1/8-strength Hoagland solution (n3).

For each treatment, five replicates were set up and total 180 plastic pots were used for this experiment. Initially, water level was maintained at two water depth levels i.e. 5 cm water depth and 15 cm water depth by adding tap water was for a week to ensure the plant survival. After that, treatment has been started through fluctuation of water depth levels by maintained the water level static at 5S and at 15S and fluctuated up to 5 cm with a 10 cm amplitude and from 15 cm to 25 cmwith a 10 cm amplitude. The nutrients solution was reformed two times in a week. Plants were harvested after 8-weeks of the treatments.

Measurement of biomass, leaf area and specific leaf area

About five-plants were selected from each treatment for the measurement of biomass. The measurements chosen for biomass traits analysis were above ground biomass (AGBm) and below ground biomass (BGBm). AGBm and BGBm were measured by using weighing scale. Leaf area (LA) were measured by analysis the images though ImageJsoftware (National Institutes of Health, USA). The specific leaf area (SLA) was calculated according to following equation:

$$S{L}_{A}=\frac{{L}_{A}}{{L}_{DW}}$$
(1)

SLA is specific leaf area; LA is leaf area per leaf; and LDW is the leaf dry weight per leaf

Measurement of relative competition index

Relative competition index (RCI) was calculated based on the total dry weight of a plant. It was the response of both invasive W. trilobata and its native W. chinensis under mono and mixed-culture. The RCI is appropriate for evaluating the interactions between these two species either positive or negative. The RCI was calculated by using the following equations57:

$$RCIa=(Xab-Xa)/(Xab+Xa)$$
(2)
$$RCIb=(Xba-Xb)/(Xba+Xb)$$
(3)

Where, X is the total dry weight of a plant, while a and b represent the both species separately, Xa show the total dry weight of species a (native W. chinensis) when grown alone, and Xb is the total dry weight of species b (invasive W. trilobata) when is grown alone. Xab is the total dry weight of species a when is grown with species b, and Xba is the total dry of species b when is grown with species a.

Measurement of plasticity index

Plasticity index (PI) ranged from zero to one and was calculated between the two levels of more affected treatment for each growth and physiological traits. The following equation was used to measure PI:

$${PI}=\frac{{Maximum}\,{value}-{Minimum}\,{value}}{{Maximum}\,{value}}$$
(4)

It can be calculated for each treatment, for each variable and for each species as the difference between the maximum value and minimum value between the two levels of each treatment divided by the maximum value13.

Measurement of net photosynthetic rate, leaf nitrogen and photosynthetic nitrogen use efficiency

The physiological parameters selected for measurements were net photosynthetic rate (Pn), leaf nitrogen (Ln) and photosynthetic nitrogen use efficiency (PNUE). Pn was measured by using a portable LI-6400XT, Lincoln, USA photosynthesis measurement system. All these data were recorded during full sunshine at 9:30–11:30 a.m. once a week during the experiment. Leaves were selected from five plants per group of treatment for the measurements.

Leaf nitrogen (Ln) was measured using the plant chlorophyll meter, Oakoch OK-Y104 (made in China). The Ln was noted from the same leaves which were used for photosynthetic measurements. While, PNUE was calculated as the ratio of Pn values to the Ln values58.

Statistical analysis

A mixed model was used to evaluate the effect of the independent variables of species, water depth fluctuations, nutrient treatments and their interaction under mono and mixed culture on the dependent variables Pn, Ln, PNUE, LA, SLA, AGBm, BGBm, PI and RCI, respectively. Pot number was used as random factor of the model. Post hoc analyses were performed using the Tukey test with P < 0.05, was used to evaluate the effect of each treatment on all parameters. Student Newman Keuls test was used for multiple comparison in case of PI. All analysis was conducted in SPSS: 22 (SPSS Inc., IL, USA) and graph were produced in origin pro9.