Nitrogen immobilization may reduce invasibility of nutrient enriched plant community invaded by Phragmites australis


Nutrient enrichment, particularly nitrogen, is an important determinant of plant community productivity, diversity and invasibility in a wetland ecosystem. It may contribute to increasing colonization and dominance of invasive species, such as Phragmites australis, especially during wetland restoration. Providing native species a competitive advantage over invasive species, manipulating soil nutrients (nitrogen) may be an effective strategy to control the invasive species and that management tool is essential to restore the degraded ecosystems. Therefore, we examined competition between Phragmites australis and Melaleuca ericifolia in a greenhouse setting with activated carbon (AC) treatments, followed by cutting of Phragmites shoots in nutrient-rich soils. Additionally, we evaluated the effect of AC on plant-free microcosms in the laboratory, to differentiate direct effects of AC on soil microbial functions from indirect effects. Overall, the objective was to test whether lowering nitrogen might be an effective approach for reducing Phragmites invasion in the wetland. The AC reduced Phragmites total biomass more significantly in repeated cut regime (57%) of Phragmites shoots compared to uncut regime (39%). Conversely, it increased Melaleuca total biomass by 41% and 68% in uncut and repeated cut regimes, respectively. Additionally, AC decreased more total nitrogen in above-ground biomass (41 to 55%) and non-structural carbohydrate in rhizome (21 to 65%) of Phragmites, and less total nitrogen reduction in above-ground biomass (25 to 24%) of Melaleuca in repeated cut compared to uncut regime. The significant negative correlation between Phragmites and Melaleuca total biomass was observed, and noticed that Phragmites acquired less biomass comparatively than Melaleuca in AC-untreated versus AC-treated pots across the cutting frequency. AC also caused significant changes to microbial community functions across Phragmites populations, namely nitrogen mineralization, nitrification, nitrogen microbial biomass and dehydrogenase activity (P ≤ 0.05) that may potentially explain changes in plant growth competition between Phragmites and Melaleuca. The overall effects on plant growth, however, may be partially microbially mediated, which was demonstrated through soil microbial functions. Results support the idea that reducing community vulnerability to invasion through nutrient (nitrogen) manipulations by AC with reducing biomass of invasive species may provide an effective strategy for invasive species management and ecosystem restoration.


There are numerous global environmental issues ranging from climate change, global warming, pollution, biological invasion to loss of biodiversity and many more1. Amongst these, biological invasion has been considered the most persistent issue to cause biodiversity loss and species extinction placing negative impacts on natural communities and ecological characteristics2,3. In parallel, nutrient enrichment is augmenting the invasion process, and is considered a communal obstacle in implementing plant community restoration initiatives4. Human-induced fertilization due to industrialization5, atmospheric nitrogen deposition through air pollution6, and invasion by N-fixing shrubs7 can influence the increase in soil nutrients, in particular N availability. As a result, the nutrient enrichment in soil can benefit fast-growing invasive plant species, that outperform the native slow-growing plant species and invade into native ecosystems8. Wetlands, including brackish marshes, represent one of the most productive natural habitats9 supporting various biological communities and biogeochemical functions. These provide heterogeneous nutrient conditions and diverse habitats, which can play as one of the key drivers to global nutrient cycling9,10. Additionally, topographic features of wetlands make these ecosystems vulnerable to human-induced disturbances11, thereby, facilitating invasion of non-native plants, and even some native plants play dominating role into the ecosystem.

Invasion of Phragmites australis (hereafter Phragmites) possess the great threat amongst aggressive and widely studied invasive plants in wetlands12,13. It significantly modifies and often destroys ecosystem structure and functions14,15,16,17. Physiological characteristics of Phragmites including high rates of reproduction, well-developed aerenchyma and rhizosphere facilitate colonization, and dense canopies related to their high productivity can inhibit germination and growth of neighbour plant species18,19,20. The tissue chemistry of Phragmites and its extensive production alters nutrient pools21 and availability in soils16,18. Together with its negative effects on ecology, Phragmites can impose considerable financial loss22. For example, invasive species management costs about $25 billion/year in the USA23. Globally, there are numerous wetland restoration projects related to Phragmites invasion representing significant cost to the USA, Canada and Australia24,25,26. Though invasiveness is dependent upon genotypes, for example, a Eurasian genetic lineage is considered as an invader in North America27 and Phragmites has been considered a cryptic invader creating management problems for scientists and land managers28,29. The invasive plant management project is generally lacking scientific information regarding invasion mechanism of the targeted species. For example, Phragmites is considered a cryptic invader, it may lack specific information related to invasion mechanisms, though it depneds on its context30. Current methods to control Phragmites invasions are aimed at eradication of existing populations, which are effective only in short term31. The recent study raises the question about the efficacy of managing large populations invaded by Phragmites through the method22. Generally, Phragmites populations can be treated using herbicide applications in combination with cutting, burning and covering with plastic32. Phragmites populations may quickly re-sprout from rhizome and seed bank reserves after the treatments33, indicating it requires long-term monitoring and re-treatment until native vegetation can be restored. Some recent studies showed seeds compared to vegetative propagules may play an important role to reproduce the Phragmites colonization27. Thus, repeating control measures indefinitely to address recurring Phragmites invasions is not only expensive, and time consuming, but also interferes with native plant community establishment34.

There are many studies supporting the assertion that nutrient enrichment favours invasiveness and long-term persistence of the invader in wetland native plant communities making the community more susceptible to be invasible35,36,37. The approach to ecosystem management like Phragmites invaded ecosystems, focus on simply eradicating Phragmites stands rather than nutrient management38,39 and restoring native plant communities32. Again, very few studies have been conducted systematically on community invasibility to compare the effects of disturbance regimes40 and how management approaches may work effectively on promoting re-establishment of neighbouring plant species4. Therefore, we hypothesized that creating conditions through nutrient (nitrogen) manipulation in soil followed by frequent cuttings of Phragmites shoots may favour associated plant species Melaleuca ericifolia (hereafter Melaleuca) over Phragmites that would be a more operative approach to reduce invasions by Phragmites. The Melaleuca has been selected as an alternative plant for wetland restoration because distribution and abundance of this indigenous plant has reduced sharply due to high salinity, nutrient enrichment, flooding and invasion along the entire coastal zone of Australia, especially southern-eastern Australia39,41,42. Thus, the rehabilitation of those wetlands is the priority of the natural resource management agencies (government and private) in Australia43,44. This hypothesis is associated with the resource–ratio hypothesis, that explains plant community composition influenced by relative abundance of limiting resources in soil45,46. Thus, the resource (nutrient) manipulation limits the availability to the target dominating plant species, but it may benefit the desired native species47. Our previous studies support the idea that nutrient enrichment, specifically high nitrogen (N) availability, can facilitate Phragmites invasion into wetlands and thereby, suppress the associated plant species Melaleuca39. In addition to N enrichment, increased phosphorus may play an important role to displace the slow-growing native plants by fast-growing invasive plants in many ecosystems including wetland ecosystems48,49. But, in particular, N enrichment in the wetland is the key driver to play community invasibility because a large part of N is being deposited in wetlands through surface runoff and ground water50. Thus, Phragmites is highly responsive to N availability and it attains a competitive advantage under these conditions39 similar to plant species Rumex confertus51.

The key matter in restoration with nutrient-enriched ecosystems is to deal with the question of how the slower growing native species may benefit in competition over fast-growing invasive species52,53. Till now, there is no conclusive assertion about the successful mechanisms of invasive species and the susceptibility of plant communities to invasion54,55. Therefore, documentation of species-specific invasion mechanism, its effects and control into invaded plant communities is more reasonable and methodical than on general theories for all invasive species54,56,57. In addition, relatively very little research has focused on the effects of control measures of the invasive species, for example, Phragmites on the rhizome and rhizosphere soil that influence plant productivity, and likely contribute to competitive advantages over native plant species58. Therefore, we questioned whether depletion of rhizome reserves via shoot cutting and changes in rhizosphere soil characteristics through soil nitrogen immobilization via activated carbon (AC) amendment might be the key to control of Phragmites in its invaded communities. Activated carbon addition to soil generally reduces nitrogen availability to plants59. The general assumption is that AC reduces inorganic nitrogen content in soil such as NO3 and NH460 which are mostly available for plant growth and they may limit growth and productivity of plant61. The underlying mechanism is that addition of AC leads to nitrogen immobilization through greater microbial N uptake62, but it depends on soil characteristics63. The general understanding is that limiting N availability to plant through immobilization may reduce the productivity of the invasive plant, and thereby, increasing the growth of native ones, which also depends on the response of the plant to N availability in soil64.

Therefore, we conducted greenhouse experiments to test whether management approaches in nutrient enriched condition may increase the competitive ability of Melaleuca over Phragmites into a wetland plant community. Additionally, a laboratory soil incubation experiment was conducted to test whether AC-induced changes to soil microbial functions via nitrogen immobilization could be helpful to explain the changes in plant growth in the above experiments. Our precise objectives were to (i) study the interactive effects of AC amendment in growth substrate and repeated shoot cutting of Phragmites on the competitional growth between Phragmites and Melaleuca, and (ii) assess whether responses of plant productivity and resources (carbohydrate storage, nitrogen concentration) to AC addition and subsequent cutting of Phragmites shoots were mediated by N immobilization via microbial interactions. More specifically, the experiments were conducted to test whether AC addition followed by repeated cutting of Phragmites shoots either individually or combinedly could facilitate Melaleuca success given sufficient competition over Phragmites.

Materials and Methods

Study species

Phragmites australis is a cosmopolitan and successional species that is distributed all over the world (except Antarctica), and still it remains unclear about its originality in many regions of the earth21. It has been considered as a weedy and invasive population in North America, Australia, and Madagascar65,66,67. Phragmites is widely-dominated across most parts of temperate regions of Australia65. It forms mostly dense monospecific stands in fresh and coastal wetlands, freshwater swamps and lakes, along rivers, and even in irrigation canals68. On the other hand, Melaleuca is a native shrub or small tree with a maximum height 8 m, is distributed in coastal and near coastal freshwater and brackish-water wetlands across southeastern Australia44. Most species of the genus Melaleuca are reliant on seed alone for reproduction; however, Melaleuca can form clonal stands through the production of ramets69. These two species naturally coexist in most of the wetlands in south-eastern Australia70,71.

Greenhouse studies

Collection of plant materials

Methods for the greenhouse experiments were followed according to our previous works39,42 with modifications in treatments. Briefly, in September 2012, we collected rhizomes of Phragmites from Cherry Lake (37°51′30″S, 144°50′5″E), that is a coastal wetland in Altona, Melbourne, Victoria, Australia72. Cherry Lake was a low land and seasonally inundated marshy area before European settlement, but following urbanization, it was altered and drained to manage the wetland. During European settlement, Phragmites occupied a small portion of the wetland, but gradually, it has been expanding vigorously and making almost monospecific stands that changes the floristic composition16. Considered a less-disturbed and low-nutrient wetland39, the site was selected to source plant materials. We used the live rhizome for the experiment consisting of only one active node. We purchased 6-month old Melaleuca seedlings from a commercial source, grown from locally collected seeds in potting mix soil42.

Soil preparation

We used circular 7 L plastic pots (25 × 22 × 17-cm) containing 4 L substrate. We prepared the substrate with 1:7 ratio of river sand and potting mix respectively, including nutrient addition treatment (3 g/L) nutrient level. The composition of the potting mix was organic materials, living organisms, minerals and nutrients (see ‘availability of materials and data’ for more information). The used nutrient was the mixed pelletized fertilizer with a ratio of N-P-K: 16-8-9 and it was used to enrich nutrient level. In addition, a 50 mL of soil from mixed population of Phragmites and Melaleuca in Edithvale wetland (described below in details) was added to the substrate for introduction of microbes. This soil was also used for a later field soil incubation experiment. We mixed soil (river sand & potting mix) with inoculum and nutrients appropriately in isolated pots by hand, placing the mixture into targeted plastic pots, then used for transplantation of the excised rhizomes of Phragmites.

Experimental design and measurement

To examine the interactive effects of AC amendment in soil substrate and repeated shoot cutting of Phragmites on competition between experimental plants in nutrient enriched condition, we initially manipulated the substrate pots with AC (activated charcoal powder made from coconut shell) [with (70 g/L substrate) and without AC (0 g/L)] and nutrient (3 g/L). The manipulated pots were then subjected to nutrient addition at a rate of 3 g/L in the tilled topsoil monthly. Plants were arranged in treatment pots as Phragmites alone, Melaleuca alone, and Melaleuca with Phragmites with five replicates. The management strategies of the experimental pots were: (a) Phragmites alone and Melaleuca alone (b) Phragmites plus Melaleuca without cutting of Phragmites shoots, (c) Phragmites plus Melaleuca subjected to one time Phragmites shoot cutting at 6 weeks during the 6-month experimental period, and (d) Phragmites plus Melaleuca with two times Phragmites shoot cuttings by a 6-week interval from commencement of the experiment until termination.

We transplanted the collected live rhizomes of Phragmites and Melaleuca seedlings into prepared experimental pots as soon as possible to avoid damage to the plant materials. The experimental pots were placed in a natural lit greenhouse, with a condition of 23 ± 3 °C and 12 ± 2 °C day/night temperature. We used an auto irrigation system to water the experimental pots and maintained soil moisture at 55 ± 5%, with a weekly soil moisture monitoring system. We randomized the experimental pots weekly by cleaning other seedlings except Phragmites and Melaleuca. We applied a destructive approach for biomass measurement and collected each individual of Phragmites and Melaleuca after 6 months of their growing for measurement of above-ground biomass (AGB) and below-ground biomass (BGB). Rhizome of Phragmites was collected for total non-structural carbohydrate (TNC) content to justify the role of carbohydrate for vegetative success of Phragmites. In addition to this, total nitrogen (TN) concentration in above-ground tissue of both species was measured to differentiate the nitrogen assimilation by both of the species.

Laboratory incubation studies using field soil

Investigating AC-induced changes to soil nitrogen cycling rate and microbial activities [soil microbial biomass nitrogen (SMB-N) and dehydrogenase activity (DHA)] may be helpful explaining the changes in plant growth, as determined in the above experiment. The experiment was conducted in laboratory using nutrient enriched field soil and it was plant-free microcosms experiment to differentiate direct versus indirect effects of AC on the soil microbial functions. This was due to AC influencing soil effects on plant growth through allelochemicals absorption secreted by Phragmites42,68 and altering plant growth. We collected 15 soil cores from three high nutrient enriched Phragmites invaded populations in the Edithvale wetland (38°05′54.2′′S 145°08′24.8′′E) in December 2016. The wetland is located in south-eastern Melbourne which is listed as Ramsar site on August 2001. The Edithvale wetland is a mud-flat habitat, which is considered as high nutrient enriched soil and adversely impacted by urban development39,73. The main source of wetland nutrient enrichment is related to urban stormwater including industrial and agricultural runoff74. The soil was considered for this soil incubation experiment due to its high nutrient-enriched characteristics. The collected soil amended with and without AC was examined to compare how AC may change soil nitrogen cycling and microbial activities to understand the roles of nitrogen immobilization and microbial functions in controlling the competitiveness between Phragmites and Melaleuca in the above greenhouse studies.

The five invaded cores from each of the considered Phragmites population were collected and each individual core was kept in separate Ziploc bags. The samples were immediately transported to the laboratory with a laboratory ice box. Soils of the five replicates in each population were homogenised by sorting all debris and sieving (<2 mm). Before treatment, five subsamples of soil (10 g each) were collected from each composite and immediately extracted with 50 mL of 2.0 M KCl for the initial determination of extractable ammonium and nitrate. To half of the soil from each population, 70 g/L AC (the amount used for above greenhouse studies) was mixed into the soil. All soils with and without AC were rearranged in 5 replicates into the new plastic soil pot and maintained 50% soil moisture by tap water that was compatible with the field water-holding capacity. Then, the plastic soil pots were kept in dark at 22 °C for 30 days to simulate microbial activities and functions. After 30 days, the soils were removed, and subsamples were taken for specific laboratory analyses.

Laboratory analysis

We used ion chromatograph to measure ammonium and nitrate concentrations in all soil extracts (Shimadzu Ion Chromotograph, Kyoto, Japan) following the method of Maynard et al.75. Net mineralization of N was calculated as extractable nitrate (NO3) + ammonium in the incubated sample minus extractable nitrate + ammonium in the initial extracts. Net nitrification was calculated as extractable nitrate in the incubated sample minus extractable nitrate in the initial extracts. Microbial biomass nitrogen (MBN) and dehydrogenase activity (DHA) in treated soil were determined according to the procedures of Uddin & Robinson71. The alkaline persulfate oxidation method was used to determine the total nitrogen in above-ground plant tissue of the above greenhouse experimental samples of both species following the method proposed by Purcell & King76. We used phenol-sulphuric acid method for TNC measurement in Phragmites rhizome of the greenhouse experiment77.

Statistical analyses

We applied analysis of variance (ANOVA) and nested ANOVA to assess the effects Phragmites, AC and Phragmites shoots cuttings on the measured variables of Melaleuca. In the case of Melaleuca, the model comprised of main effects of Phragmites & AC (effect of one of the independent variables on the dependent variables), and their interactions. In addition, the effects of cuttings of Phragmites shoots (nested within Phragmites), the cutting frequency of Phragmites shoots (nested within cutting), and their interactions with AC also formed the part of the model, which was analysed by the statistical methods of Uddin et al.42. In case of Phragmites, we used ANOVA models that included only cutting treatments of Phragmites, AC and their interactions. One-way ANOVA with LSD tests were used to compare the multiple means among treatments for different measured parameters of Phragmites and Melaleuca. We also used ANOVAs to examine the effects of AC addition on soil extractable nitrate and ammonium concentration, net mineralization and nitrification, microbial biomass-N, and DHA in the field soil incubation experiment. The model used included Phragmites populations and AC, and their interactions. Again, we used Real Statistics Resource Pack (Software plug-in, Microsoft Excel 2010) to investigate if the difference in slopes of regressions between AC treatments was statistically significant78. Furthermore, independent sample t-test was conducted to compare soil nitrogen indices within each population. We also applied Levene’s test of equality to check the homogeneity of variance of the used data (square root transformed if necessary) for both of Phragmites and Melaleuca. We considered P ≤ 0.05 as significant for all experimental data analyses by using statistical software IBM SPSS statistics 24.0.


Plant responses to activated carbon and shoot cuttings of Phragmites

The aboveground and belowground biomass of Melaleuca was negatively affected significantly by competition with Phragmites (Table 1, Fig. 1A,B). The average Melaleuca AGB decreased from 692.24 ± 37.38 to 32.29 ± 1.03 g/m2 and 6399.55 ± 34.09 to 45.02 ± 2.06 g/m2 between mono (only Melaleuca) and mixed uncut cultures (Phragmites and Melaleuca grown together), either AC-untreated or AC-treated, respectively (Fig. 1A,B). In case of BGB, it reduced from 205.02 ± 16.55 to 9.92 ± 0.44 g/m2 and 180.94 ± 9.74 to 14.61 ± 0.90 g/m2 respectively (Fig. 1A,B). AC had no significant growth effect on Melaleuca in mono-culture whereas it had significant effect on mixed uncut cultures (Fig. 1A,B). Again, AC had significant negative growth effect on Phragmites in both mono and mixed uncut cultures (Table 2, Fig. 2A,B). The AGB and BGB of Phragmites was reduced from 1979.88 ± 79.81 to 1290.37 ± 50.95 g/m2 and 2311.22 ± 95.40 to 1660.33 ± 77.55 g/m2 between mono and mixed uncut cultures without and with AC, respectively. The addition of AC had different outcomes on the competitive interactions between Phragmites and Melaleuca biomass, but it was noticed that Melaleuca growth increased due to AC in uncut regime (Figs. 1 and 2). The interactive effects of AC and Phragmites were significant effect on biomass of Melaleuca (Table 1).

Table 1 Results of ANOVA and nested ANOVA analysing treatments of Phragmites, activated carbon, and management strategies of Phragmites (cutting of Phragmites shoots) on dry weight of aboveground biomass (AGB), belowground biomass (BGB), total biomass (TB), and total nitrogen (TN) concentration of AGB of Melaleuca.
Figure 1

Effects of management strategies of Phragmites (cuttings of Phragmites shoots) either in AC-untreated or AC-treated on (A) above-ground biomass (g/m2), and (B) below-ground biomass(g/m2) of Melaleuca growing single or mixed with Phragmites in experimental pots. Each bar is the mean ± SE (n = 5). Different letters in each bar indicate significantly differences (P ≤ 0.05).

Table 2 Results of ANOVA and nested ANOVA analysing treatments of activated carbon and management strategies of Phragmites (cutting of Phragmites shoots) on dry weight of aboveground biomass (AGB), belowground biomass (BGB), total biomass, total nitrogen (TN) concentration of AGB and total non-structural carbohydrate (TNC) of rhizome in Phragmites growing in experimental communities with Melaleuca.
Figure 2

Effects of management strategies of Phragmites (cuttings of Phragmites shoots) either in AC-untreated or AC-treated on (A) Above-ground biomass (g/m2), and (B) below-ground biomass (g/m2) of Phragmites growing single, or mixed with Melaleuca in the experimental pots. Each bar is the mean ± SE (n = 5). Different letters in each bar indicate significantly differences (P ≤ 0.05).

The cutting had significant negative effect on biomass of Phragmites, and consequently, it increased biomass of Melaleuca (Tables 1 and 2, and Figs. 1 and 2). The single Phragmites shoot cuttings reduced 29% (4152.37 ± 100.48 to 2938.37 ± 129.03 g/m2) & 36% (2512.69 ± 158.87 to 1607.14 ± 50.44 g/m2) total biomass of Phragmites and increased 60% (42.20 ± 1.25 to 67.71 ± 4.34 g/m2) & 69% (59.63 ± 2.90 to 100.90 ± 5.02 g/m2) total biomass of Melaleuca in without and with AC, respectively (Figs. 1 and 2). Again, double shoot cuttings of Phragmites reduced 51% & 65% total biomass of Phragmites and increased 115% & 157% total biomass of Melaleuca in without and with AC, respectively (Figs. 1 and 2). The same cutting had also significant effects on biomass of Phragmites and Melaleuca in AC-untreated and AC-treated experimental pots (Figs. 1 and 2) (P ≤ 0.05).

Total nitrogen concentration in above-ground biomass of Phragmites was greater than Melaleuca (Fig. 3A,B). TN concentration of Melaleuca was negatively affected significantly with Phragmites competition and AC treatments (Table 1). Cutting and cutting frequency of Phragmites shoots also significantly increased the TN concentration of Melaleuca among mixed cultures, whereas the TN concentration of Phragmites was decreased with both AC-untreated and AC-treated cultures (Fig. 3A,B), but however, no significant interactions between AC and cutting regimes were found (Table 1). The average Melaleuca TN concentration was reduced from 31.72 ± 0.90 to 8.17 ± 0.42 mg/g with competition of Phragmites without AC, which was 74%, whereas with AC it was 72% (22.20 ± 0.58 to 6.09 ± 0.28 mg/g). Again, cutting of the Phragmites shoots has significant positive effect in increasing the TN concentration of Melaleuca, which was an average from 8.17 ± 0.42 to 13.77 ± 0.43 mg/g without AC and 6.09 ± 0.28 to 10.06 ± 0.42 mg/g with AC, whereas TN concentration of Phragmites was reduced from 40.55 ± 0.71 to 24.59 ± 0.48 mg/g without AC and 23.90 ± 0.49 to 11.19 ± 0.74 mg/g with AC.

Figure 3

Effects of management strategies of Phragmites (cuttings of Phragmites shoots) either in AC-untreated or AC-treated on Total nitrogen (TN) concentration (mg/g) of (A) Melaleuca and (B) Phragmites in above-ground biomass growing single, or mixed with Melaleuca in the experimental pots. Each bar is the mean ± SE (n = 5). Different letters in each bar indicate significantly differences (P ≤ 0.05).

The concentrations of TNC in Phragmites rhizomes strongly differed between the treatments (Table 2, Fig. 4). The imposed management regimes affected the levels of TNC, and TNC concentrations were significantly higher at without AC than with AC. Single shoot cuttings of Phragmites reduced 32% (111.88 ± 3.05 to 76.46 ± 3.03 mg/g) & 46% (88.19 ± 2.75 to 47.41 ± 2.62 mg/g) TNC concentration in without and with AC respectively, whereas they were 53% & 79% for double shoot cuttings (Fig. 4). However, cutting of Phragmites shoot had significant negative effects on TNC at both levels of AC. There were no competition effects on TNC at both AC levels (Table 2), but significant interactions between AC and cutting management were found for TNC indicates that the effects of these management regimes were effective (Table 2).

Figure 4

Effects of management strategies of Phragmites (cuttings of Phragmites shoots) either in AC-untreated or AC-treated on total non-structural carbohydrate (TNC) (mg/g) of Phragmites rhizome growing single, or mixed with Melaleuca in the experimental pots. Each bar is the mean ± SE (n = 5). Different letters in each bar indicate significantly differences (P ≤ 0.05).

Relationships among measured variables

There was significant negative correlation between Phragmites and Melaleuca total plant biomass in all experimental pots (Fig. 5A). It was observed that Phragmites acquired greater biomass in AC-untreated pots compared to AC-treated pots across the cutting frequency (Fig. 5A). In contrast, Melaleuca showed the opposite scenario regarding biomass accumulation. The significant difference was found between slopes of the regression lines of AC-untreated and AC-treated pots (t = 3.47) with df 26 and α 0.05, and the stronger negative correlation was noticed in AC-untreated pots (F = 57.12, df = 1,12, p > 0.001; r2 = 0.85) compared to AC-treated pots (F = 36.55, df = 1,12, p > 0.001; r2 = 0.76) (Fig. 5A). Again, a significant positive relationship between aboveground biomass and total nitrogen concentration of Melaleuca and Phragmites in mixed culture both in AC-untreated and AC-treated was found, but the responses were different (Fig. 5B,C). The significant difference was found between slopes of the regression lines of AC-untreated and AC-treated pots for Melaleuca (t = 3.38) (Fig. 5B), but not for Phragmites (t = 0.5) with df 26 and α 0.05 (Fig. 5C). The most positive relationships were found for Phragmites (AC-untreated: F = 45.19, df = 1,12, p > 0.001, r2 = 0.79; AC-treated: F = 39.44, df = 1,12, p > 0.001; r2 = 0.76) compared to Melaleuca (AC-untreated: F = 31.24, df = 1,12, p > 0.001, r2 = 0.72; AC-treated: F = 27.75, df = 1,12, p > 0.001; r2 = 0.69) both in AC-untreated and AC-treated mixed cultures (Fig. 5B,C). Furthermore, it was found that there was a significant positive correlation between below-ground biomass of Phragmites and total non-structural carbohydrates in both AC-untreated and AC-treated mixed communities (Fig. 5D). The slope difference between AC-untreated and AC-treated was significant (t = 2.69) with df 26 and α 0.05 that indicates AC had a significant effect in influencing the carbohydrate storage in rhizomes (Fig. 5D). The stronger positive relation was noted in AC-treated pots (F = 131.17, df = 1,12, p > 0.001; r2 = 0.91) compared to AC-untreated pots (F = 75.77, df = 1,12, p > 0.001; r2 = 0.86) (Fig. 5D). Again, the strong positive relationship between TN concentration of AGB and TNC level of BGB in Phragmites was noticed in AC-untreated (F = 67.36, df = 1,12, p > 0.001; r2 = 0.85) compared to AC-treated (F = 49.97, df = 1,12, p > 0.001; r2 = 0.82) mixed communities (Fig. 5E), but the slope difference was not significant (t = 1.85) with df 26 and α 0.05.

Figure 5

Regression analyses between (A) total biomass of Phragmites and Melaleuca; (B) above-ground biomass (AGB) of Melaleuca and total nitrogen (TN) concentration of AGB Melaleuca; (C) above-ground biomass (AGB) of Phragmites and total nitrogen (TN) concentration of AGB Phragmites; (D) below-ground biomass (BGB) of Phragmites and total non-structural carbohydrate (TNC) of Phragmites rhizome; and (E) total nitrogen (TN) concentration of AGB Phragmites and total non-structural carbohydrate (TNC) of Phragmites rhizome grown in mixed (Phragmites and Melaleuca together) cultures whether Phragmites subjected to different management strategies (cuttings of Phragmites shoots) either in AC-untreated or AC-treated experimental pots.

Soil responses to activated carbon

Concentrations of extractable NO3-N and NH4-N were greatly reduced in pots treated with AC relative to unamended pots at the end of the experiment in all populations (Table 3, Fig. 6A,B). Soils amended with AC reduced an average 19% and 17% NO3−N and NH4-N respectively. The reductions of NO3-N were from 66.07 ± 1.03 to 54.72 ± 1.59 mg/kg, 57.09 ± 1.21 to 45.89 ± 1.00 mg/kg and 58.28 ± 1.97 to 47.45 ± 1.82 mg/kg in population_1, population_2 and population_3 respectively (Fig. 6A). The NH4-N was reduced by an order of scale, from 12.24 ± 0.45 to 9.94 ± 0.34 mg/kg, 9.77 ± 0.36 to 7.70 ± 0.17 mg/kg, 10.01 ± 0.55 to 8.57 ± 0.10 mg/kg in population_1, population_2 and population_3 respectively (Fig. 6B). AC addition decreased both net N mineralization and net N nitrification significantly, which was on an average 77% and 73% respectively compared to without AC pots in all populations (Table 3, Fig. 6C,D), but Phragmites population reduced significantly only net N mineralization (Table 3). Microbial biomass N was significantly higher in AC unamended pots than amended pots, which were 40.81, 38.59 & 44.28% increment in population_1, population_2 and population_3, respectively (Table 3, Fig. 7A). However, the microbial biomass N was significantly influenced by Phragmites populations, but there is no significant interaction between AC and populations (Table 3). The microbial biomass N decreased on an average 41% at AC-amended soil compared to AC unamended soil. Dehydrogenase activity was also significantly lower in the AC-amended soil by an average 43.57% than in the AC-unamended soil (Fig. 7B). AC-amendment decreased dehydrogenase activity most significantly in population_2 among three populations (Fig. 7B). The overall reduction of dehydrogenase activity indicated a decrease in the microbial metabolism in the soil due to less mineralization and nitrification rate in the AC-amended soil (Table 3, Fig. 6C,D). All parameters except net nitrification in soil significantly varied across the AC-amendment and populations but no interactive effects (AC × Phragmites populations) were observed (Table 3).

Table 3 Results of ANOVA analysing treatments of activated carbon, Phragmites population, and their interactions on soil nitrate (NO3N), ammonium (NH4+-N), microbial biomass nitrogen (MB-N), and dehydrogenase activity (DHA) in nutrient enriched Phragmites invaded soil.
Figure 6

Extractable (A) nitrate and (B) ammonium concentrations, (C) net nitrogen (N) mineralization rate, and (D) net nitrification rate in activated carbon (AC) unamended and amended pots of different populations. Each bar is the mean ± SE (n = 5). Different letters in each bar indicate significantly differences (P ≤ 0.05).

Figure 7

Soil (A) microbial biomass nitrogen (SMB-N) and (B) dehydrogenase activity in activated carbon (AC) unamended and amended pots of different populations. Each bar is the mean ± SE (n = 5). Different letters in each bar indicate significantly differences (P ≤ 0.05).


Plant responses

In nutrient-enriched wetlands, Phragmites seedlings and adult plants grow larger and produce more stems, florets, inflorescences and thus, seeds with rhizome, further benefiting the invasion79. We hypothesized that reducing nitrogen availability in nutrient-rich soil via AC addition followed by Phragmites shoot cuttings may reduce Phragmites growth, and thereby, may favour growth of associate plant species Melaleuca. So, controlling growth of Phragmites in nutrient-rich wetlands, our experimental results demonstrate that AC-amended soil followed by Phragmites shoot cuttings increased competitiveness of Melaleuca over Phragmites growth (Fig. 1). On the contrary, Phragmites competitively overwhelmed Melaleuca growth in AC unamended soil (Fig. 1), which is aligned with other studies in prairie restoration80. The AC additions in our studies reduced biomass of Phragmites that indicates the reduction of invasibility of the plant community invaded by Phragmites. Conversely, AC increased biomass of Melaleuca in mixed culture, which suggest that AC had negative impact on Phragmites allowing Melaleuca to be more competitive.

Our results are largely consistent with the fluctuating resource hypothesis of invasibility proposed by Davis et al.81, whom suggests that a plant community is more susceptible to invasion when there is an increase in the amount of unused resources. This condition also increases the relative competitive ability of invasive species in a plant community82. In our experimental results, the increase of Melaleuca biomass in AC-amended mixed cultures indicated a relatively low positive outcome because Melaleuca is a tree with lengthy lifespan, it requires longer time to achieve more biomass than Phragmites, a perennial grass. Melaleuca had also better growth (shown in single growth experiment) suggesting that with the correct growth condition, it would successfully establish in its community. As a result, it can be said Melaleuca may establish and grow properly in Phragmites-dominated wetland ecosystems with AC-amendment followed by reducing biomass of Phragmites.

The success of the establishment of plants depends on mechanisms, and the mechanisms are species-specific and contextual83. It is difficult to establish a single management approach to an ecological restoration initiative, requiring integrated control measures to restore the degraded ecosystem. This would be practical if the targeted plant, for example, Phragmites has persistent communities84. In our studies, however, only the AC addition reduced Phragmites biomass and increased Melaleuca biomass, but AC with cutting of Phragmites shoots enhanced the magnitude of reduction for Phragmites biomass. Subsequently, this approach increased the biomass of Melaleuca more significantly suggesting combined management (AC with cuttings of shoots) was more effective than only AC addition to reduce the invasibility of the community by Phragmites. Melaleuca experienced comparatively less impact by Phragmites in AC-amended pots compared with AC-unamended cutting treatments pots (Fig. 1). It may imply that AC-induced low N availability in soil had less effect on the competitive ability of Melaleuca and Phragmites. It is assumed that Melaleuca achieved benefits to establishment and growth in cutting experiments with AC-amendment through nitrogen immobilization, which was also effective in reducing Phragmites competitive ability. Thus, our results were compatible with findings of Perry et al.85 whom found lowering N availability through carbon amendment reduced the competitive ability of invasive species, Phalaris arundinacea. As a result, we can assume that the effects of AC addition with repetitive cutting of Phragmites shoot on Melaleuca growth is explained through N immobilization.

The increasing trend of total N concentration in AGB of Melaleuca and decreasing level in Phragmites AGB among treatments indicates that AC associated with cuttings of Phragmites shoots offered competitive ability of Melaleuca by up-taking more available nitrogen over Phragmites. This is aligned with other studies, that found invasive species attained comparatively less nitrogen content than native in the used treatments85,86. We also examined the effects of treatments on carbohydrates reserves in Phragmites rhizome that allow Phragmites to re-sprout in the next spring growth. The treatments reduced significantly Phragmites biomass (above and belowground) and carbohydrate reserves in rhizome. Additionally, our laboratory incubation experiment showed that AC also had direct impact on soil N availability. This assumes that it might be a basic function of both N-availability in soil and carbohydrate reserve in rhizome for competitive advantage of Phragmites in the plant community. This implies Phragmites establishment and growth might be restricted by carbohydrate reserve in rhizome and N-availability in soil. This finding is aligned with the studies of Kleijn et al.87, whom found available soil N supplemented by stored carbohydrate reserves was responsible for vegetative success of Veratrum album.

The negative correlation between Phragmites and Melaleuca total biomass (Fig. 5A), and the more reduction of Melaleuca biomass in AC-untreated compared to AC-treated experimental pots (Fig. 1A,B) indicates that AC with cutting of Phragmites shoots may promote the productivity of Melaleuca, which is aligned other studies62. The studies found carbon amendment reduced N availability in soil, and thereby, reduced competition between native and exotic plant, and provided benefit to the native. The more positive relationship between nitrogen concentration and above-ground biomass in Phragmites (Fig. 5B,C) indicates responses of Phragmites to N availability was greater than Melaleuca, which may provide it indirect benefit. Melaleuca however, may experience less negative effects than Phragmites for the reduction of N availability, which is supported by the studies of Alpert and Maron88 and Alpert64. They found carbon addition may reduce ecosystem invasiblity by invasive grass through lowering nitrogen availability and promoting native plants growth for ecosystem restoration.

Furthermore, AC treatment with cuttings influence TNC levels of rhizomes indicates that the management options may work in combination to slowly reduce carbohydrate reserves of Phragmites rhizome, thus ultimately negatively influencing the sprouting for the next growth. The results are aligned with the studies of Moyo et al.89, whom found cutting management had significant negative effect on TNC level. The reducing level was amplified with cutting frequency that ultimately affected shoot production. Additionally, the positive relationships among rhizome biomass, TNC of Phragmites rhizome and TN concentration of Phragmites AGB (Fig. 5D,E) indicate that reducing rhizome biomass through cutting and AC-amendment may act as a negative driver to re-sprout for Phragmites, which ultimately provides benefits to Melaleuca. The findings are similar with other studies of Druege et al.90 whom found nitrogen concentration and TNC level are positively correlated, and cutting frequency may reduce TNC level in Chrysanthemum plant species.

Soil responses

In our study, extractable inorganic N concentrations (nitrate and ammonium concentrations) were lower in AC pots relative to unamended pots, consistent with the studies of Blumenthal et al.59 and Morghan et al.91, where addition of AC as sucrose and/ or sawdust has shown reduced soil inorganic N levels, though the efficacy depends on initial soil fertility, quantity and form of AC added. Again, our results showed that AC additions stimulated microbial N-immobilization by reducing rates of net N mineralization and net nitrification, which is consistent with the findings of Torok et al.92, who found nitrogen immobilization by carbon acts to stimulate the restoration process in a grassland community. The results of our laboratory incubation are compatible to explain the underlying mechanism of nitrogen cycling in the first plant community experiment as the N level in the used field soil for incubation experiment was high39.

The MBN significantly decreased in the AC-amended soil in all populations in our study, which is supported by other studies93,94. For example, Zhang et al.93 found the MBN decreased with AC addition at a rate of 4.5 t/ha/yr in the field at most sampling dates and soil depths compared to the unamended soil treatment, whereas Zavalloni et al.95 and Dempster et al.96 found AC amendment had no significant impact on MBN. Again, AC increased soil MBC in our studies supported by Ma et al.97 and Gebhardt et al.98 whom found addition of carbon as a soil amendment significantly increased MBC and thereby, altered plant biomass. Therefore, the increased MBC and decreased MBN indicates that AC in soil acted as a carbon source rather than a nitrogen source for microbes in soil substrates. As a result, this had a significant influence on N cycling, for example, increasing microbial N immobilization, which is also aligned with our results. AC is not only responsible for reducing soil N level, but it may work in soil through different mechanisms. For example, some studies assumed that AC changes plant growth by sequestering allelochemicals, that was found in previous Phragmites studies including ours42, and altering microbial functions through changes of microbial communities99,100. In this case, soil DHA may be used as an indicator of overall soil microbial activity101. In our study, AC caused direct changes to soil microbial functions, which were observed in our plant-free microcosms laboratory incubation experiment. Our studies showed AC decreased DHA compared to unamended soil for each population, which might be linked to decreasing the microbial symbionts associated with Phragmites success, which is explained by Centaurea species to support this argument102,103.

Mechanisms involved in reducing invasibility

It is common for soil-N availability to influence positively for rapid shoot growth in plant and ultimately, increasing plant biomass39,87. In AC-amended soil, Melaleuca attained relatively higher biomass and N level with increasing cutting frequency of Phragmites shoots, whereas Phragmites experienced a lower level. This implies N-poor soil might be a good condition for the competitive ability of Melaleuca. It also indicates that N-use efficiency of Melaleuca in AC-amended soil would be higher than Phragmites, which was also supplemented by the Phragmites shoot cuttings. The findings of our studies are compatible with Perry et al.85, whom found native plant Carex hystericina achieved greater N-uptake and biomass compared to invasive species Phalaris arundinacea in carbon-treated soil. Again, Chapin et al.104 found both nutrient level in soil and carbohydrate reserves play an important role to establishment of the plant, but the rapid growth is regulated completely by carbohydrate reserves. In this case, our results support the idea that reduced carbohydrate and nitrogen level in AC-amendment followed by Phragmites shoot cuttings influenced negatively the competitive ability and plant growth of Phragmites, whereas it allowed Melaleuca the opportunity to grow and establish.

Furthermore, it is assumed that N availability in soil and carbohydrate reserve in rhizome are responsible in facilitating Phragmites invasion and to completing its growing season in the short term. In our study, it appeared that while shoot cutting with AC treatments significantly reduced carbohydrates simultaneously of Phragmites, the remaining carbohydrate reserves may act as a survivor for the next spring growth. This was noted in another study related to perennial Veratrum album by Schaffner et al.105. So, it is important to continue the process until next growing season of Phragmites, but it is subject to context to making the approach effective in control of Phragmites in nutrient enriched condition.

Implications for Phragmites control

Melaleuca growth improvement over Phragmites in AC-amended soil followed by cutting treatments suggests that this condition lowered soil N availability through N-immobilization that reduced Phragmites growth. This situation is shown between Phragmites and Melaleuca interactions, and requires further research to demonstrate the interactions between other associated plant species and Phragmites in wetlands within this condition. Creating N-immobilization in Phragmites dominated wetland restoration technique needs active reduction of soil N availability by using AC. Additionally, N availability in wetlands may be reduced by frequent cutting of Phragmites shoots before starting a restoration initiative, which supports the studies of Verhoeven & Schmitz106, whom found frequent mowing was effective in lowering the nutrient condition, that controls the plant growth8. Nitrogen immobilization technique via activated carbon has potential to reduce invasibility and provide positive effect on native plant growth in ecological restoration initiatives107,108. The challenge is however, that this restoration technique needs higher amount of AC for larger scale implications, thus entailing higher cost. Maintaining the reduced N-availability in soil presents additional challenge, as many environmental processes (mineralization) and factors (surface runoff due to agriculture & industrialization) actively work to increase the N-inputs in wetlands. For this reason, it is essential to develop a new technique to reduce nitrogen level in Phragmites dominated wetland, which is partially supplemented by frequent shoot cutting of Phragmites. The minimum level of AC required for lowering N level in wetland soil prior to restoration initiative also needs to be determined, though it is contextual. Furthermore, it is essential to prevent the N-source to Phragmites dominated wetlands, which can be manipulated through vegetation buffering and landscaping109. Further study is recommended to investigate the wide range of N-assimilation between Melaleuca and Phragmites under this condition to find out the difference amongst them.


Our past studies39 showed Phragmites is more dominating in nutrient-rich compared to nutrient-poor condition which provides further evidence in supporting the hypothesis that nutrient enrichment facilitates invasion of  Phragmites. Based on this scenario, this study demonstrated whether nutrient (nitrogen) manipulation may provide a competitive advantage to Melaleuca over Phragmites that might be an operative and effective restoration tool to restore the Phragmites-dominated wetlands. Our results suggest that AC addition in soil followed by frequent Phragmites shoot cuttings may provide competitive advantage for Melaleuca over Phragmites. Additionally, it is  assumed that soil nitrogen immobilization due to AC addition may be responsible for Phragmites growth reduction leading to facilitating Melaleuca growth. However,  soil inorganic nitrogen availability was not measured in the plant microcosms experiment, but it was addressed by plant-free microcosms and supported by the studies of Perry et al.85 whom found inorganic nitrogen was reduced in carbon-enriched soil by 10 to 30 mg/kg in a competitive experiment between invasive Phalaris arundinacea and a native sedge Carex hystericina. Furthermore, Torok et al.92,110 found immobilization of soil nitrogen by carbon addition was effective for the sandy grassland restoration. To the best of our knowledge, these types of experimental studies regarding Phragmites management are the first where nutrient (nitrogen) manipulation through AC followed by Phragmites shoot cuttings have demonstrated the examination of competitive ability between Phragmites and associated native species, further explained by microbial interactions that may mediate the growth of native over dominating species Phragmites.

Data availability

Data will be available where applicable.


  1. 1.

    Kowarsch, M. et al. A road map for global environmental assessments. Nat. Clim. Change 7, 379–382, (2017).

    ADS  Article  Google Scholar 

  2. 2.

    Mack, R. N. et al. Biotic invasions: causes, epidemiology, global consequences, and control. Ecol Appl 10, 10.1890/1051-0761(2000)010[0689:bicegc];2 (2000).

  3. 3.

    Wilcove, D. S., Rothstein, D., Dubow, J., Phillips, A. & Losos, E. Quantifying threats to imperiled species in the United States. Biosci. 48, 607–615 (1998).

    Article  Google Scholar 

  4. 4.

    Corbin, J. D. & D’Antonio, C. M. Can Carbon Addition Increase Competitiveness of Native Grasses? A Case Study from California. Restor. Ecol. 12, 36–43, (2004).

    Article  Google Scholar 

  5. 5.

    Vitousek, P. M., Mooney, H. A., Lubchenco, J. & Melillo, J. M. Human domination of Earth’s ecosystems. Sci. 277, 494–499 (1997).

    CAS  Article  Google Scholar 

  6. 6.

    Bobbink, R. Effects of nutrient enrichment in Dutch chalk grassland. J. Appl. Ecol., 28–41 (1991).

  7. 7.

    Maron, J. L. & Connors, P. G. A native nitrogen-fixing shrub facilitates weed invasion. Oecologia 105, 302–312 (1996).

    ADS  Article  Google Scholar 

  8. 8.

    Maron, J. L. & Jeffries, R. L. Restoring enriched grasslands: Effects of mowing on species richness, productivity, and nitrogen retention. Ecol. Appl. 11, 1088–1100,[1088:regeom];2 (2001).

    Article  Google Scholar 

  9. 9.

    Mitsch, W. & Gosselink, J. (John Wiley and Sons, New York, NY, USA, 2007).

  10. 10.

    Costanza, R. et al. The value of the world’s ecosystem services and natural capital. Nat. 387, 253–260 (1997).

    CAS  ADS  Article  Google Scholar 

  11. 11.

    Zedler, J. B. & Kercher, S. Causes and consequences of invasive plants in wetlands: opportunities, opportunists, and outcomes. Crit. Rev. Plant. Sci. 23, 431–452 (2004).

    Article  Google Scholar 

  12. 12.

    Uddin, M. N., Caridi, D. & Robinson, R. W. Phytotoxic evaluation of Phragmites australis: an investigation of aqueous extracts of different organs. Mar. Freshw. Res. 63, 777–787 (2012).

    CAS  Article  Google Scholar 

  13. 13.

    Benoit, L. K. & Askins, R. A. Impact of the spread ofPhragmites on the distribution of birds in Connecticut tidal marshes. Wetl. 19, 194–208, (1999).

    Article  Google Scholar 

  14. 14.

    Mills, E. L., Strayer, D. L., Scheuerell, M. D. & Carlton, J. T. Exotic species in the Hudson River basin: a history of invasions and introductions. Estuaries 19, 814–823 (1996).

    Article  Google Scholar 

  15. 15.

    McCormick, M. K., Kettenring, K. M., Baron, H. M. & Whigham, D. F. Extent and reproductive mechanisms of Phragmites australis spread in brackish wetlands in Chesapeake Bay, Maryland (USA). Wetl. 30, 67–74 (2010).

    Article  Google Scholar 

  16. 16.

    Uddin, M. N., Robinson, R. W., Buultjens, A., Al Harun, M. A. Y. & Shampa, S. H. Role of allelopathy of Phragmites australis in its invasion processes. J. Exp. Mar. Biol. Ecol. 486, 237–244, (2017).

    Article  Google Scholar 

  17. 17.

    Price, A. L., Fant, J. B. & Larkin, D. J. Ecology of Native vs. Introduced Phragmites australis (Common Reed) in Chicago-Area Wetlands. Wetl. 34, 369–377, (2014).

    Article  Google Scholar 

  18. 18.

    Meyerson, L. A., Saltonstall, K., Windham, L., Kiviat, E. & Findlay, S. A comparison of Phragmites australis in freshwater and brackish marsh environments in North America. Wetl. Ecol. Manage. 8, 89–103, (2000).

    CAS  Article  Google Scholar 

  19. 19.

    Mozdzer, T. J. & Zieman, J. C. Ecophysiological differences between genetic lineages facilitate the invasion of non‐native Phragmites australis in North American Atlantic coast wetlands. J. Ecol. 98, 451–458 (2010).

    Article  Google Scholar 

  20. 20.

    Guo, W. Y., Lambertini, C., Li, X. Z., Meyerson, L. A. & Brix, H. Invasion of Old World Phragmites australis in the New World: precipitation and temperature patterns combined with human influences redesign the invasive niche. Glob. Change Biol. 19, 3406–3422 (2013).

    Google Scholar 

  21. 21.

    Pysek, P. et al. Physiology of a plant invasion: biomass production, growth and tissue chemistry of invasive and native Phragmites australis populations. Preslia 91, 51–75, (2019).

    Article  Google Scholar 

  22. 22.

    Quirion, B., Simek, Z., Davalos, A. & Blossey, B. Management of invasive Phragmites australis in the Adirondacks: a cautionary tale about prospects of eradication. Biol. Invasions 20, 59–73, (2018).

    Article  Google Scholar 

  23. 23.

    Pimentel, D., Zuniga, R. & Morrison, D. Update on the environmental and economic costs associated with alien-invasive species in the United States. Ecol. Econ. 52, 273–288 (2005).

    Article  Google Scholar 

  24. 24.

    Silliman, B. R., Grosholz, E. & Bertness, M. D. Human impacts on salt marshes: a global perspective. (Univ of California Press, 2009).

  25. 25.

    Streever, W. J. Trends in Australian wetland rehabilitation. Wetl. Ecol. Manage. 5, 5–18, (1997).

    Article  Google Scholar 

  26. 26.

    Van der Putten, W. H. Die-back of Phragmites australis in European wetlands: an overview of the European Research Programme on Reed Die-back and Progression (1993–1994). Aquat. Bot. 59, 263–275, (1997).

    Article  Google Scholar 

  27. 27.

    Kettenring, K. M. & Mock, K. E. Genetic diversity, reproductive mode, and dispersal differ between the cryptic invader, Phragmites australis, and its native conspecific. Biol. Invasions 14, 2489–2504 (2012).

    Article  Google Scholar 

  28. 28.

    Kristin, S. Cryptic invasion by a non-native genotype of the common reed, Phragmites australis, into North America. PNAS 99, 2445–2449 (2002).

    Article  Google Scholar 

  29. 29.

    Kiviat, E. et al. Evidence does not support the targeting of cryptic invaders at the subspecies level using classical biological control: the example of Phragmites. Biological Invasions, 1–13, (2019).

  30. 30.

    Walker, L. R., J. Walker & Hobbs, R. J. Linking Restoration and Ecological Succession. Vol. 1976 (Springer, 2007).

  31. 31.

    Rohal, C. B., Kettenring, K. M., Sims, K., Hazelton, E. L. G. & Ma, Z. Surveying managers to inform a regionally relevant invasive Phragmites australis control research program. J. Environ. Manag. 206, 807–816, (2018).

    CAS  Article  Google Scholar 

  32. 32.

    Hazelton, E. L., Mozdzer, T. J., Burdick, D. M., Kettenring, K. M. & Whigham, D. F. Phragmites australis management in the United States: 40 years of methods and outcomes. AoB plants 6 (2014).

  33. 33.

    Saltonstall, K., Burdick, D., Miller, S. & B., S. Native and Introduced Phragmites: Challenges in Identification, Research, and Management of the Common Reed. National Estuarine Research Reserve Technical Report Series (2005).

  34. 34.

    Marks, M., Lapin, B. & Randall, J. Phragmites australis (P. communis): threats, management and monitoring. Nat. Areas J. 14, 285–294 (1994).

    Google Scholar 

  35. 35.

    Crawley, M. J. et al. The population biology of invaders. Philos. Trans. R. Soc. Lond. B: Biol. Sci. 314, 711–731 (1986).

    ADS  Article  Google Scholar 

  36. 36.

    Hobbs, R. J. & Atkins, L. Effect of disturbance and nutrient addition on native and introduced annuals in plant communities in the Western Australian wheatbelt. Austral Ecol. 13, 171–179 (1988).

    Article  Google Scholar 

  37. 37.

    Vallano, D. M., Selmants, P. C. & Zavaleta, E. S. Simulated nitrogen deposition enhances the performance of an exotic grass relative to native serpentine grassland competitors. Plant. Ecol. 213, 1015–1026, (2012).

    Article  Google Scholar 

  38. 38.

    Kettenring, K. M., McCormick, M. K., Baron, H. M. & Whigham, D. F. Mechanisms of Phragmites australis invasion: feedbacks among genetic diversity, nutrients, and sexual reproduction. J. Appl. Ecol. 48, 1305–1313, (2011).

    Article  Google Scholar 

  39. 39.

    Uddin, M. N. & Robinson, R. W. Can nutrient enrichment influence the invasion of Phragmites australis? Sci. Total. Environ. 613, 1449–1459, (2018).

    CAS  ADS  Article  Google Scholar 

  40. 40.

    Pearson, D. E., Ortega, Y. K., Eren, O. & Hierro, J. L. Community Assembly Theory as a Framework for Biological Invasions. Trends Ecol. Evolution 33, 313–325, (2018).

    Article  Google Scholar 

  41. 41.

    Bowkett, L. A. & Kirkpatrick, J. B. Ecology and conservation of remnant Melaleuca ericifolia stands in the Tamar Valley, Tasmania. Australian J. Botany 51, 405–413, (2003).

    Article  Google Scholar 

  42. 42.

    Uddin, M. N., Robinson, R. W., Caridi, D. & Al Harun, M. A. Y. Suppression of native Melaleuca ericifolia by the invasive Phragmites australis through allelopathic root exudates. Am. J. Botany 101, 479–487, (2014).

    Article  Google Scholar 

  43. 43.

    de Jong, N. H. Woody plant restoration and natural regeneration in wet meadow at Coomonderry Swamp on the south coast of New South Wales. Mar. Freshw. Res. 51, 81–89, (2000).

    Article  Google Scholar 

  44. 44.

    Raulings, E. J. et al. Rehabilitation of Swamp Paperbark (Melaleuca ericifolia) wetlands in south-eastern Australia: effects of hydrology, microtopography, plant age and planting technique on the success of community-based revegetation trials. Wetlands Ecology and Management 15, (2007).

  45. 45.

    Tilman, D. Resource competition and community structure. (Princeton university press, 1982).

  46. 46.

    Liu, L. et al. Nutrient enrichment alters impacts of Hydrocotyle vulgaris invasion on native plant communities. Scientific Reports 6, 39468,, (2016).

  47. 47.

    Tilman, E. A., Tilman, D., Crawley, M. J. & Johnston, A. Biological weed control via nutrient competition: potassium limitation of dandelions. Ecol. Appl. 9, 103–111 (1999).

    Article  Google Scholar 

  48. 48.

    Bertness, M. D., Ewanchuk, P. J. & Silliman, B. R. Anthropogenic modification of New England salt marsh landscapes. Proc. Natl Acad. Sci. 99, 1395–1398 (2002).

    CAS  ADS  Article  Google Scholar 

  49. 49.

    Brooks, M. L. Effects of increased soil nitrogen on the dominance of alien annual plants in the Mojave Desert. J. Appl. Ecol. 40, 344–353 (2003).

    Article  Google Scholar 

  50. 50.

    Brinson, M. M. & Malvárez, A. I. Temperate freshwater wetlands: types, status, and threats. Environ. Conserv. 29, 115–133 (2002).

    Article  Google Scholar 

  51. 51.

    Kolodziejek, J. Growth and competitive interaction between seedlings of an invasive Rumex confertus and of co-occurring two native Rumex species in relation to nutrient availability. Scientific Reports 9, (2019).

  52. 52.

    Corbin, J. D. & D’Antonio, C. M. Competition between native perennial and exotic annual grasses: implications for an historical invasion. Ecol. 85, 1273–1283 (2004).

    Article  Google Scholar 

  53. 53.

    Prober, S. M., Thiele, K. R., Lunt, I. D. & Koen, T. B. Restoring ecological function in temperate grassy woodlands: manipulating soil nutrients, exotic annuals and native perennial grasses through carbon supplements and spring burns. J. Appl. Ecol. 42, 1073–1085, (2005).

    CAS  Article  Google Scholar 

  54. 54.

    Rodgers et al. Ready or not, garlic mustard is moving in: Alliaria petiolata as a member of eastern North American forests. Bioscience 58, 426–436 (2008).

  55. 55.

    Richardson, D. M. & Pyšek, P. Plant invasions: merging the concepts of species invasiveness and community invasibility. Prog. Phys. Geogr. 30, 409–431, (2006).

    Article  Google Scholar 

  56. 56.

    Zheng, Y.-L. et al. Species composition, functional and phylogenetic distances correlate with success of invasive Chromolaena odorata in an experimental test. Ecol. Lett. 21, 1211–1220, (2018).

    Article  Google Scholar 

  57. 57.

    Wavrek, M., Heberling, J. M., Fei, S. & Kalisz, S. Herbaceous invaders in temperate forests: a systematic review of their ecology and proposed mechanisms of invasion. Biol. Invasions 19, 3079–3097, (2017).

    Article  Google Scholar 

  58. 58.

    Kowalski, K. P. et al. Advancing the science of microbial symbiosis to support invasive species management: a case study on Phragmites in the Great Lakes. Frontiers in Microbiology 6, (2015).

  59. 59.

    Blumenthal, D. M., Jordan, N. R. & Russelle, M. P. Soil carbon addition controls weeds and facilitates prairie restoration. Ecological Applications 13, 605–615, doi:10.1890/1051-0761(2003)013[0605:scacwa];2 (2003).

  60. 60.

    Rowe, H. I., Brown, C. S. & Paschke, M. W. The Influence of Soil Inoculum and Nitrogen Availability on Restoration of High-Elevation Steppe Communities Invaded by Bromus tectorum. Restor. Ecol. 17, 686–694, (2009).

    Article  Google Scholar 

  61. 61.

    Carlisle, E., Myers, S., Raboy, V. & Bloom, A. The effects of inorganic nitrogen form and CO2 concentration on wheat yield and nutrient accumulation and distribution. Frontiers in Plant Science 3, (2012).

  62. 62.

    Averett, J. M., Klips, R. A., Nave, L. E., Frey, S. D. & Curtis, P. S. Effects of Soil Carbon Amendment on Nitrogen Availability and Plant Growth in an Experimental Tallgrass Prairie Restoration. Restor. Ecol. 12, 568–574, (2004).

    Article  Google Scholar 

  63. 63.

    Cabrera, M. L., Kissel, D. E. & Vigil, M. F. Nitrogen mineralization from organic residues: Research opportunities. J. Environ. Qual. 34, 75–79, (2005).

    CAS  Article  PubMed  PubMed Central  Google Scholar 

  64. 64.

    Alpert, P. Amending invasion with carbon: after fifteen years, a partial success. Rangel. 32, 12–15 (2010).

    Article  Google Scholar 

  65. 65.

    Packer, J. G., Meyerson, L. A., Skalova, H., Pysek, P. & Kueffer, C. Biological Flora of the British Isles: Phragmites australis. J. Ecol. 105, 1123–1162, (2017).

    Article  Google Scholar 

  66. 66.

    Hocking, P. J., Finlayson, C. M. & Chick, A. J. The biology of Australian weeds. 12. Phragmites australis (Cav.) Trin. ex Steud. Australian Inst. Agric. Sci. J. 49, 123–132 (1983).

    Google Scholar 

  67. 67.

    Srivastava, J., Kalra, S. J. S. & Naraian, R. Environmental perspectives of Phragmites australis (Cav.) Trin. Ex. Steudel. Appl. Water Sci. 4, 193–202, (2014).

    CAS  ADS  Article  Google Scholar 

  68. 68.

    Rudrappa, T. et al. Phragmites australis root secreted phytotoxin undergoes photo-degradation to execute severe phytotoxicity. Plant. Signal. Behav. 4(6), 506–513 (2009).

    CAS  Article  Google Scholar 

  69. 69.

    Robinson, R. W., Boon, P. I., Sawtell, N., James, E. A. & Cross, R. Effects of environmental conditions on the production of hypocotyl hairs in seedlings of Melaleuca ericifolia (swamp paperbark). Australian J. Botany 56, 564–573 (2008).

    Article  Google Scholar 

  70. 70.

    Morris, K., Boon, P. I., Raulings, E. J. & White, S. D. Floristic shifts in wetlands: the effects of environmental variables on the interaction between Phragmites australis (Common Reed) and Melaleuca ericifolia (Swamp Paperbark). Mar. Freshw. Res. 59, 187–204 (2008).

    Article  Google Scholar 

  71. 71.

    Uddin, M. N. & Robinson, R. W. Responses of plant species diversity and soil physical-chemical-microbial properties to Phragmites australis invasion along a density gradient. Sci. Rep. 7, 11007 (2017).

    ADS  Article  Google Scholar 

  72. 72.

    Relf, M. & New, T. Conservation needs of the Altona skipper butterfly, Hesperilla flavescens flavescens Waterhouse (Lepidoptera: Hesperiidae), near Melbourne, Victoria. J. Insect Conserv. 13, 143–149, (2009).

    Article  Google Scholar 

  73. 73.

    Greet, J. & Rees, P. Slashing may have potential for controlling Phragmites australis in long-inundated parts of a Ramsar-listed wetland. Ecol. Manag. Restor. 16, 233–236, (2015).

    ADS  Article  Google Scholar 

  74. 74.

    Lane, B., Bezuijen, M., Orscheg, C., Todd, J. & Carr, G. Edithvale–Seaford Wetlands Ramsar Management Plan. Unpublished report for Melbourne Waterways and Drainage Group. Ecology Australia Pty Ltd, Fairfield, Victoria (2000).

  75. 75.

    Maynard, D., Kalra, Y. & Crumbaugh, J. Nitrate and exchangeable ammonium nitrogen. Soil sampling and methods of analysis 1 (1993).

  76. 76.

    Purcell, L. C. & King, C. A. Total nitrogen determination in plant material by persulfate digestion. Agron. J. 88, 111–113, (1996).

    CAS  Article  Google Scholar 

  77. 77.

    Uddin, M. N., Robinson, R. W. & Caridi, D. Phytotoxicity induced by Phragmites australis: an assessment of phenotypic and physiological parameters involved in germination process and growth of receptor plant. J. Plant. Interact. 9, 338–353, (2014).

    CAS  Article  Google Scholar 

  78. 78.

    Zaiontz, C. Real statistics using Excel,[accessed on 10 October 2016] (2014).

  79. 79.

    King, R. S., Deluca, W. V., Whigham, D. F. & Marra, P. P. Threshold effects of coastal urbanization onPhragmites australis (common reed) abundance and foliar nitrogen in Chesapeake Bay. Estuaries Coasts 30, 469–481 (2007).

    CAS  Article  Google Scholar 

  80. 80.

    Green, E. K. Department of Horticultural Science, U. o. M., 305 Alderman Hall, 1970 Folwell Avenue, St Paul, MN 55108, USA, Galatowitsch, S. M. & Department of Horticultural Science, U. o. M., 305 Alderman Hall, 1970 Folwell Avenue, St Paul, MN 55108, USA Effects of Phalaris arundinacea and nitrate‐N addition on the establishment of wetland plant communities. J. Appl. Ecol. 39, 134–144, (2018).

    Article  Google Scholar 

  81. 81.

    Davis, M. A., Grime, J. P. & Thompson, K. Fluctuating resources in plant communities: a general theory of invasibility. J. Ecol. 88, 528–534 (2000).

    Article  Google Scholar 

  82. 82.

    Shea, K. & Chesson, P. Community ecology theory as a framework for biological invasions. Trends Ecol. Evol. 17, 170–176 (2002).

    Article  Google Scholar 

  83. 83.

    Engst, K., Baasch, A. & Bruelheide, H. Predicting the establishment success of introduced target species in grassland restoration by functional traits. Ecol. Evolution 7, 7442–7453, (2017).

    Article  Google Scholar 

  84. 84.

    Stylinski, C. D. & Allen, E. B. Lack of native species recovery following severe exotic disturbance in southern Californian shrublands. J. Appl. Ecol. 36, 544–554, (1999).

    Article  Google Scholar 

  85. 85.

    Perry, L. G., Galatowitsch, S. M. & Rosen, C. J. Competitive control of invasive vegetation: a native wetland sedge suppresses Phalaris arundinacea in carbon‐enriched soil. J. Appl. Ecol. 41, 151–162 (2004).

    CAS  Article  Google Scholar 

  86. 86.

    McLendon, T. & Redente, E. F. Effects of nitrogen limitation on species replacement dynamics during early secondary succession on a semiarid sagebrush site. Oecologia 91, 312–317, (1992).

    ADS  Article  Google Scholar 

  87. 87.

    Kleijn, D., Treier, U. A. & Muller-Scharer, H. The importance of nitrogen and carbohydrate storage for plant growth of the alpine herb Veratrum album. N. Phytologist 166, 565–575, (2005).

    CAS  Article  Google Scholar 

  88. 88.

    Alpert, P. & Maron, J. L. Carbon Addition as a Countermeasure Against Biological Invasion by Plants. Biol. Invasions 2, 33–40, (2000).

    Article  Google Scholar 

  89. 89.

    Moyo, H., Scholes, M. C. & Twine, W. The effects of repeated cutting on coppice response of Terminalia sericea. Trees-Structure Funct. 29, 161–169, (2015).

    CAS  Article  Google Scholar 

  90. 90.

    Druege, U., Zerche, S., Kadner, R. & Ernst, M. Relation between nitrogen status, carbohydrate distribution and subsequent rooting of chrysanthemum cuttings as affected by pre-harvest nitrogen supply and cold-storage. Ann. Botany 85, 687–701, (2000).

    CAS  Article  Google Scholar 

  91. 91.

    Morghan, K. J. R. & Seastedt, T. R. Effects of Soil Nitrogen Reduction on Nonnative Plants in Restored Grasslands. Restor. Ecol. 7, 51–55, (1999).

    Article  Google Scholar 

  92. 92.

    Torok, K. et al. Immobilization of soil nitrogen as a possible method for the restoration of sandy grassland. Appl. Vegetation Sci. 3, 7–14, (2000).

    Article  Google Scholar 

  93. 93.

    Zhang, Q. Z. et al. Effects of Biochar on Soil Microbial Biomass after Four Years of Consecutive Application in the North China Plain. Plos One 9, (2014).

  94. 94.

    Durenkamp, M., Luo, Y. & Brookes, P. C. Impact of black carbon addition to soil on the determination of soil microbial biomass by fumigation extraction. Soil. Biol. Biochem. 42, 2026–2029, (2010).

    CAS  Article  Google Scholar 

  95. 95.

    Zavalloni, C. et al. Microbial mineralization of biochar and wheat straw mixture in soil: A short-term study. Appl. Soil. Ecol. 50, 45–51, (2011).

    Article  Google Scholar 

  96. 96.

    Dempster, D. N., Gleeson, D. B., Solaiman, Z. M., Jones, D. L. & Murphy, D. V. Decreased soil microbial biomass and nitrogen mineralisation with Eucalyptus biochar addition to a coarse textured soil. Plant. Soil. 354, 311–324, (2012).

    CAS  Article  Google Scholar 

  97. 97.

    Ma, L. N., Huang, W. W., Guo, C. Y., Wang, R. Z. & Xiao, C. W. Soil Microbial Properties and Plant Growth Responses to Carbon and Water Addition in a Temperate Steppe: The Importance of Nutrient Availability. Plos One 7, (2012).

  98. 98.

    Gebhardt, M., Fehmi, J. S., Rasmussen, C. & Gallery, R. E. Soil amendments alter plant biomass and soil microbial activity in a semi-desert grassland. Plant. Soil. 419, 53–70, (2017).

    CAS  Article  Google Scholar 

  99. 99.

    Kulmatiski, A. Changing Soils to Manage Plant Communities: Activated Carbon as a Restoration Tool in Ex-arable Fields. Restor. Ecol. 19, 102–110, (2011).

    Article  Google Scholar 

  100. 100.

    Wurst, S. & van Beersum, S. The impact of soil organism composition and activated carbon on grass-legume competition. Plant. Soil. 314, 1–9, (2009).

    CAS  Article  Google Scholar 

  101. 101.

    Gu, Y., Wang, P. & Kong, C. Urease, invertase, dehydrogenase and polyphenoloxidase activities in paddy soil influenced by allelopathic rice variety. Eur. J. Soil. Biol. 45, 436–441 (2009).

    CAS  Article  Google Scholar 

  102. 102.

    Callaway, R. M., Thelen, G. C., Barth, S., Ramsey, P. W. & Gannon, J. E. Soil fungi alter interactions between the invader centaurea maculosa and north american natives. Ecol. 85, 1062–1071, (2004).

    Article  Google Scholar 

  103. 103.

    Kulmatiski, A. & Beard, K. H. Activated carbon as a restoration tool: potential for control of invasive plants in abandoned agricultural fields. Restor. Ecol. 14, 251–257 (2006).

    Article  Google Scholar 

  104. 104.

    Chapin, F. S., Schulze, E. D. & Mooney, H. A. The ecology and economics of storage in plants. Annu. Rev. Ecol. Syst. 21, 423–447, (1990).

    Article  Google Scholar 

  105. 105.

    Schaffner, U., Nentwig, W. & Brandle, R. Effect of mowing, rust infection and seed production upon c-reserves and n-reserves and morphology of the perennial veratrum-album l (liliales, melanthiaceae). Botanica Helvetica 105, 17–23 (1995).

    Google Scholar 

  106. 106.

    Verhoeven, J. T. A. & Schmitz, M. B. Control of plant-growth by nitrogen and phosphorus in mesotrophic fens. Biogeochemistry 12, 135–148, (1991).

    CAS  Article  Google Scholar 

  107. 107.

    Morghan, K. J. R. Department of Agronomy and Range Science, O. S. A., University of California, Davis, CA 95616, USA, Seastedt, T. R. & Department of Environmental, P., and Organismic Biology, and Institute of Arctic and Alpine Research, University of Colorado, 1560 30th Street, Campus Box 450, Boulder, CO 80309–0450, U.S.A. Effects of Soil Nitrogen Reduction on Nonnative Plants in Restored Grasslands. Restor. Ecol. 7, 51–55, (1999).

    Article  Google Scholar 

  108. 108.

    Paschke, M. W., McLendon, T. & Redente, E. F. Nitrogen availability and old-field succession in a shortgrass steppe. Ecosyst. 3, 144–158, (2000).

    CAS  Article  Google Scholar 

  109. 109.

    Dosskey, M. G. Toward quantifying water pollution abatement in response to installing buffers on crop land. Environ. Manag. 28, 577–598, (2001).

    CAS  Article  Google Scholar 

  110. 110.

    Torok, K. et al. Long-term outcome of nitrogen immobilization to restore endemic sand grassland in Hungary. J. Appl. Ecol. 51, 756–765, (2014).

    CAS  Article  Google Scholar 

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We would like to thank all members in our ecology group of Victoria University, Melbourne, Australia. Special thanks go to all laboratory technicians under this group to collect sample, soil preparation, planting and all other associated technical supports. In addition to this, we would like to thank the technical staff in the chemical laboratory to help for analysing the chemical parameters. Furthermore, we would like to thank the staff of Melbourne Water, Victoria, Australia, who was involved to give permission for collecting plant materials and soil samples from field for this experiment.

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M.N.U. conducted the majority of the experiments, and took the lead in analysis of the data and drafting of the manuscript. R.W.R. edited & reviewed the manuscript, gave support and conceptual advices and general supervisions. T.A. edited & reviewed the manuscript.

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Correspondence to Md Nazim Uddin.

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Uddin, M.N., Robinson, R.W. & Asaeda, T. Nitrogen immobilization may reduce invasibility of nutrient enriched plant community invaded by Phragmites australis. Sci Rep 10, 1601 (2020).

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