Search tips
Search criteria 


Logo of scirepAboutEditorial BoardFor AuthorsScientific Reports
Sci Rep. 2017; 7: 11309.
Published online 2017 September 12. doi:  10.1038/s41598-017-11707-x
PMCID: PMC5596010

Soil microbial carbon utilization, enzyme activities and nutrient availability responses to Bidens pilosa and a non-invasive congener under different irradiances


Two Bidens species (Bidens pilosa and B. bipinnata) that originate from America have been introduced widely in pan-tropics, with the former regarded as a noxious invasive weed whereas the latter naturalized as a plant resource. Whether the two species exhibit different effects on the belowground system remains rarely studied. This study was conducted to investigate soil microbial carbon (C) utilization, enzyme activities and available nitrogen, phosphorus and potassium contents under the two species in a subtropical garden soil of southern China under different levels of light intensity. Results showed that the microbial C utilization and enzyme activities were not significantly different under the two species, implying that the strong invasiveness of B. pilosa could not be due to the plant-soil microbe interactions, at least plant-induced alterations of microbial community function to utilize C substrates. Alternatively, available soil nitrogen and potassium contents were significantly higher under B. pilosa than under B. bipinnata in full sun, indicating that the strong invasiveness of B. pilosa could result from rapid nutrient mobilizations by B. pilosa. However, the differences turned non-significant as light intensity decreased, suggesting that light availability could substantially alter the plant effects on soil nutrient mobilizations.


Biological invasion has received growing concerns, because a deal of previous studies reported its negative effects on ecosystem properties1, 2. Alien plants can greatly change ecosystem properties and ecological processes such as soil carbon (C)/nitrogen (N) cycling, soil microbial community, and soil organic matter and litter decomposition in invaded habitats, consequently influencing stabilization of ecosystem functions3, 4. Hundreds of million dollars are spent to prevent from and control biological invasion each year5, but it remains a global environmental issue because of its harms to native species and environment in invaded ecosystems. Therefore, considerable attentions have been focused to clarify the underlying invasion mechanisms, to observe invasion consequences and to explore effective control measures, aiming to minimize and diminish invasion effects. Nevertheless, many aspects of invasion are not completely understood yet and it remains difficult to drawn a general conclusion according to the existing knowledge1, 4, because invasion effects are often species-, ecosystem- and context- specific6, 7.

Invasive plants can change soil conditions and reconstruct soil microbial community once they invade successfully, and therefore obtain soil nutrients easier than their co-existing competitors6, 8. Although soil microbial community may be structurally robust to environmental changes9, establishment of invasive plants can alter the soil microbial community composition1012 and abundance of several microbial functional groups1315. This could be due to invasion-induced changes in plant or/and soil properties. Invasive plants could have higher growth rate and productivity and therefore high C inputs into soils through litterfalls and root exudates to feed soil microorganisms1618, with generally higher quality of substrates containing relatively high N content and low lignin content14. Different species exhibit eutrophic or oligotrophic characteristics and preferably utilize different kinds of substrate19, therefore resulting in altered soil microbial community compositions by plant invasion. Moreover, invasive plants could change a range of soil properties, e.g., soil pH value and organic C content12, 16, which are critical to modify soil microbial communities12, 20. In association with the changed microbial community composition21, soil microbial community functions (including soil enzyme activities involved in nutrient cycling) may also be modified10, 12. Consequently, these variations in soil microbial properties could induce changes in microbial community functioning such as C/N cycling and litter decomposition11, 13 and nutrient supplies under invasion22. Probably, such plant-soil interactions facilitate plant invasions23, 24 and thus invasion effects on soil microbial communities have received much attention.

Previous studies showed that invasive plants maintained higher growth activity25 and could therefore provide more substrate inputs into the soil for microbial activities. There exist reports that invasive species (e.g., Ambrosia artemisiifolia L. and Eupatorium adenophorum) could exhibit positive effects on soil microbial functions including C utilization capacity and extracellular enzyme activities, relative to their competitors10, 22. In a preliminary experiment, we found that the invasive Bidens pilosa could maintain a higher soil microbial biomass than the non-invasive B. bipinnata (455.4 ± 50.9 mg kg−1 vs. 322.5 ± 35.3 mg kg−1, respectively; see Fig. S1). These observations suggest that growths of invasive and non-invasive species could exert different effects on soil microbial community. Therefore, we expected that the invasive B. pilosa would maintain higher soil microbial activities than the non-invasive B. bipinnata. This could facilitate a successful invasion of alien species in new habitats with high nutrient cycling and supplies24.

Light availability is critical to a successful plant invasion26, 27. Relative to their competitors, invasive plants often have higher plasticity to obtain resources that are necessary for their growth28. They can maximize the aboveground biomass to compete for light in a nutrient-rich but light-limited environment, or invest more resources to produce the belowground biomass for nutrient absorptions in case that nutrients are limited29. As a result, invasive plants could outcompete their counterparts by adjusting the above- and below-ground C allocation very rapidly28, 30 or maintaining higher growth rate due to higher photosynthetic capacity at a low respiratory cost with C allocation unaltered31. Moreover, invasive species could reduce acceptors of light and electron transport and photochemical quantum yield through allelopathic interference and thus affect growths of those indigenous plants32. These changes may result in different inputs of organic materials to the soil by changing litterfall productivity and root exudates, and consequently maintain diverse soil microbial communities under different light intensities. Previous literature reported that invasive and non-invasive species could shade different soil microbial community, but whether these differences will be maintained under changed light conditions is still unclear. In this study, different levels of light intensity were set to observe responses of the soil microbial community functions under the invasive and non-invasive species. As light intensity decreased, plants may invest more resources to produce the aboveground components for the acquisition of light29 and consequently affect the belowground system to a less extent. Therefore, we expected that differences of soil microbial community functions under the invasive and non-invasive species would turn smaller.

Two Bidens species (B. pilosa and B. bipinnata) were chosen to use in the present study for comparisons. Although the both species originate from tropical America and has been widely introduced across tropics33 (also referring to Global Biodiversity Information Facility []), the former has been reported to extend very rapidly in pan-tropical zone and exert adverse effects on invaded ecosystems32, 34 and therefore listed as a noxious invasive weed (referring to Global Invasive Species Database [] and Invasive Species Compendium []), whereas the latter has been naturalized in introduced regions35, 36 and regarded as an important plant resource, e.g., as a medical material in China for a long time37. The two species can grow well in full sun when free of disturbances. Previous studies showed that light availability greatly affected some plant traits (such as weed germination and seedling growth rate31, 38) and the environmental consequences differently between invasive and non-invasive species32. A recent study showed that the photosynthetic rate and apparent quantum yield of B. pilosa and B. bipinnata were comparable, with several traits and function differently35. Whether the invasive B. pilosa and non-invasive B. bipinnata affect soil microbial community functions differently in introduced habitats and whether the pattern can be maintained, however, remained rarely studied.

To compare the consequences by growing invasive and non-invasive species, this study was conducted in a subtropical garden soil of southern China, with the invasive B. pilosa and non-invasive B. bipinnata planted. The primary objectives were: 1) to compare the soil microbial community functions and nutrient availability under the two species and 2) to test whether potentially different effects of the two species would turn smaller.


Effects on soil microbial C utilization pattern

Under full light intensity (100% RI) treatment, the invasive B. pilosa shaped the soil microbial communities with relatively lower microbial C utilization activity, as indicated by the lower AWCD under B. pilosa than that under the non-invasive B. bipinnata (Fig. 1). Under medium light intensity (40% RI) treatment, however, such a pattern was not maintained; an opposite trend appeared with slightly higher microbial C utilization activity under the invasive plant than its non-invasive congener. Growing B. bipinnata tended to contain soil microbial communities with relatively higher C utilization activity when light intensity was extremely low at 10% of full light intensity (Fig. 1). Nevertheless, plots did not significantly separate from each other between the two species or among the light intensity treatments (p > 0.05, Fig. 2).

Figure 1
Average well color development (AWCD) of soil microbial community under the invasive Bidens pilosa and the non-invasive B. bipinnata at different levels of light intensity. Different signals indicate the three RI treatments which are at natural condition ...
Figure 2
Scores of the first two principal components identified by principal component analysis on the carbon utilization pattern of soil microbial community. Different signals indicate the three RI treatments which are at natural condition and shaded at 40% ...

The AWCD of six groups of C substrate contained in the Biolog Eco-plate, i.e., carbohydrates, carboxylic acids, amine acids, amines, polymers and phenolic compounds, was further compared between the two plant species and among the three light intensity conditions. For all the six groups of C substrates, the microbial C utilization pattern was not significantly different between plants under each of the light intensity treatments (p > 0.05 for all, Fig. 3). As light intensity decreased, however, the soil microbial community significantly or marginally significantly decreased C substrate utilization, as indicated by the lower AWCD under low light intensity (p = 0.015 for carbohydrates, p = 0.077 for carboxylic acids, p = 0.032 for amine acids, p = 0.073 for amines, p = 0.055 for polymers, and p = 0.078 for phenolic compounds; Fig. 3).

Figure 3
Average well color development (AWCD) of the soil microbial community to utilize different groups of carbon source in the Biolog Eco-plate at the three RI treatments. Bars stand for means and error bars are standard errors (n = 3).

Effects on soil enzyme activities

Soil invertase activity was significantly lower under the invasive B. pilosa than under B. bipinnata (p < 0.05 for all the three light intensity treatments). The other three soil enzyme activities, i.e., urease, catalase and cellulase activities, were not significantly different between the two species (p > 0.05 for all, Fig. 4). For the both species, soil enzyme activities were depressed when light intensity decreased (Fig. 4). However, the changes of light intensity did not significantly alter the pattern of three of the four soil enzyme activities (except catalase with p = 0.025) between species, as indicated by the non-significant interactions between plant species and light intensity treatment (p > 0.05, Table 1).

Figure 4
Soil enzyme activities under the two species at 100%, 40% and 10% RI treatments. Bars stand for means and error bars are standard errors (n = 3). Significance levels are indicated by the p values above bars at each of the RI treatments. ...
Table 1
Summary of two-way analysis of variances on different groups of C substrates, soil enzyme activities and soil available nutrients.

Effects on soil available nutrients

With full light (100% RI) treatment, soil available N and K contents were significantly higher under B. pilosa than under B. bipinnata (p = 0.021 and 0.035, respectively; Fig. 5a,c), but soil available P was not significantly different between the two species (p = 0.118; Fig. 5b). Under 40% and 10% RI treatments, the differences of soil available N, P and K contents were not statistically significant between the two species (p > 0.05 for all; Fig. 5), although two-way ANOVAs showed that the interactions between plant species and light intensity were not statistically significant (p > 0.05 for all, Table 1). Regardless of plant species, a decrease in light intensity reduced soil available N content but increase soil available P and K content (Fig. 5).

Figure 5
Soil available nitrogen (N; a), phosphorus (P; b) and potassium (K; c) contents under the two species at 100%, 40% and 10% RI treatments. Bars stand for means and error bars are standard errors (n = 3). Significance levels are indicated ...


In the present study, the soil microbial C utilization pattern and three of the four extracellular enzyme activities were not significantly different by growing the two species (Figs 24). Although both originate from tropical America and have distributed in the pan-tropics, B. pilosa has been classified as a noxious invasive species that can extend rapidly and exhibit detrimental effects in introduced ecosystems32, 34 whereas B. bipinnata instead has been regarded as an important plant resource37. Our result suggests that alterations of microbial C and N utilizations could not be the reasons that result in severe invasion of B. pilosa in southern China34, compared with non-invasive congeners. Plant-soil interactions have been proposed as one of the potential mechanisms to explain a successful invasion of alien plant species in new habitats4, 6, 23. Although the soil microbial community has functional and structural plasticity which could make them resistant to environmental changes9, an increasing quantity of evidences demonstrate that plant invasions can modify soil microbial community composition10, 11, 13 and consequently change ecosystem processes such as litter decomposition and N cycling3, 11, 13. From an aspect of C and N cycling, invasive and non-invasive species did not shape significantly different soil microbial communities. However, our observation did not deny the possibility that plant-soil interactions may benefit to B. pilosa invasion in other ways, such as altering soil microbial community composition, increasing soil microbial biomass (also referring to Fig. S1) and stimulating soil enzyme activities12, 39. These may be different strategies to accelerate nutrient cycling as needed and thus to reinforce invasiveness of alien species in introduced ecosystems8, 24.

Although most of microbial community functions were comparable, available soil N and K contents were significantly higher under B. pilosa than under B. bipinnata in the 100% RI control (Fig. 5). This is likely associated with changes in multiple aspects of change in soil and plant characteristics, such as soil microbial biomass (Fig. S1) and nutrient contents in litter and fine root40, 41. Growing B. pilosa could substantially increase soil enzyme activities39 and similar positive effects were also reported for other invasive species42. Soil microbial biomass and enzyme activities may contribute to higher soil nutrient supplies under B. pilosa. More specifically, the alkali-hydrolyzable N content was significantly higher under the invasive B. pilosa than under the non-invasive B. bipinnata in the 100% RI control, which is accompanied with relatively higher soil microbial biomass and urea activity (Figs S1 and 4c).

Invasive species often have greater productivity than those non-invasive counterparts with higher capacity to tolerate environmental stresses25 and consequently could produce higher nutrient inputs into the soil. These processes could result in increases in soil nutrient contents such as soil N and P3, 40, 41, which is supported by our observations. When living in a resource-limited habitat with native and non-invasive species, invasive species may outcompete their competitors through rapid nutrient absorptions due to their fast-growth property41. Therefore, limited resource availability stresses and excludes those non-invasive species that have relatively lower reproduction and growth rate. This is a potential explanation for the invasion success of B. pilosa in southern China. At the preliminary stage, establishment of B. pilosa could change soil conditions (e.g., to activate more soil nutrients for its growth) to facilitate its invasion8. Invasive species could outcompete their competitors and invade successfully because they often have higher phenotypic plasticity and growth potential28. Nutrients fixed in plant tissues are returned to the soil through litterfall and root exudates, thus leading to increased contents of soil nutrients as observed in previous22, 41 and the present studies. This highlights the importance to consider potentially different effects of plant invasions with various severity on ecosystem processes and functions16, 18.

We expected that differences in those investigated variables would be smaller between the two species, because both species could prefer to invest more resources for light competition29 and therefore exhibit less effects on the belowground part. In the present study, the total and specific soil microbial activity and three of the four soil enzyme activities obviously decreased as light intensity declined (Figs 1, ,33 and and4),4), partially supporting our expectation. This is likely attributable to the decreased soil microbial biomass under low light condition (Fig. S1). Soil under low light intensity could receive lower substrate inputs due to declined plant growth31 and therefore cannot maintain a comparable soil microbial community with that in full sun, or at least the active soil microbial community26. Previous literature reported that size and functions of the soil microbial community were greatly affected by substrate supply43. However, our observation that light intensity exhibits little interactions with species (Table 1) suggests that low light intensity did not alter species-induced differences in the soil microbial community functions.

Soil had significantly higher available soil N content but lower available soil K content under high RI condition, regardless of the species (Fig. 5). The soil N pattern is consistent with that of soil urease activity (Fig. 4c), implying light-induced changes in soil enzyme activities could alter soil nutrient condition as needed. Nitrogen is a critical to plant growth, because it can be utilized to produce chlorophyll44 that fixes atmospheric C via photosynthesis. Therefore, plants could up-regulate N need to generate more chlorophyll for C assimilation as light intensity increases45. Greater N need stimulates plant to affect the associated soil system to produce more soil urease that converts organic N as inorganic N46. Unlike N that can be fixed from the atmosphere and then returned into the soil to increase soil N content, P and K cannot be easily produced and activated by plants and soil microorganisms47, 48. High light intensity stimulate plant growth31 and thus increase the P and K needs from soils. As a result, available soil P and K contents will decline under high light intensity when the P and K elements cannot be activated as rapid as they are absorbed. Moreover, the soil beneath the invasive B. pilosa had significantly higher available N and K contents than that beneath its congener in full sun (Fig. 5a,c). This pattern turned non-significant when light intensity decreased, suggesting that light availability substantially impacts the species effects on available soil nutrient condition.

In summary, the soil microbial community beneath the invasive B. pilosa was not significantly different from that beneath the non-invasive congener B. bipinnata in this study, as indicated by the non-significant soil microbial C utilization and enzyme activities. However, soil contained higher available N and K contents under B. pilosa than under B. bipinnata under full sunlight but the differences turned non-significant when light intensity decreased. This result indicates that nutrient mobilizations could have contributed to the strong invasiveness of B. pilosa, which depends greatly on light availability in invaded ecosystems. As an important resource for plant growth, light availability substantially also changed the soil microbial community functions and available soil N and K contents. Our results suggest that nutrient mobilizations could contribute to the strong invasiveness of B. pilosa relative to its non-invasive congeners. Nevertheless, plant-induced alterations of microbial C utilization pattern may not be the reasons for B. pilosa invasion.


Site description and experiment preparations

This study was conducted at the experimental and teaching farm of South China Agricultural University in Guangzhou. This region has the typical subtropical monsoon climate, with annual air temperature being 21.8 °C and annual precipitation being 1694 mm49. Most of the precipitation occurs from April to September (the wet season). This results in an obvious dry-wet season cycling each year in the study site.

On December 2011, seeds of B. pilosa and B. bipinnata were collected from wild populations at South China Agricultural University (N 23°16′, E 113°37′) and South China Botanical Garden (N 23°18′, E 113°36′) in Guangzhou, respectively. They were dried in the sun and then stored in the sealed plastic bags at 4 °C until used for incubation (around 4 months). On March 31 2012, seeds were sowed to raise seedlings using breeding beds in a greenhouse which located at College of Agriculture, South China Agricultural University. During the period, seedlings were thinned to leave enough space for the growth of each seedling after 20 days of culturing seedlings. Ten days after thinning, uniform individuals of B. pilosa and B. bipinnata which were approximately 10 cm high were transplanted in pots for the following study.

Experimental design

Sun-shelters with a size of 4 × 4 m2 were established for light intensity treatments, by means of covering black shading net with different light transmissions in the experimental and teaching farm of South China Agricultural University. Finally, three levels of relative light intensity, i.e., two sheltering treatments with 40% and 10% relative intensity (RIs) of full sunlight and the full sunlight control (100% RI), were established to explore potential roles of light availability on plant-induced effects on the soil microbial community functions and nutrient contents.

Under each light intensity treatment, three pots (40 cm diameter × 33 cm height) were used to grow seedlings of the invasive B. pilosa and another three used to grow seedlings of its congener B. bipinnata. Each pot contained 7.5 kg soil, with two individuals of each species grown. The used soil was collected from the experimental and teaching farm of South China Agricultural University in which both of the two species grew and then composited completely for the following plant cultivation. The soil organic matter was 2.1% and soil available nitrogen (N), phosphorus (P) and potassium (K) were 120.8, 96.0 and 99.7 mg kg−1, respectively. Plantation duration was 64 days and through the period, all the pots were watered per day to maintain soil water content. At the end of conditioning phase, soil samples were collected to analyze for soil microbial properties and available N, P and K contents.

Soil analyses

The assayed soil microbial community properties include microbial carbon (C) utilization pattern and soil enzyme activities. Soil microbial C utilization pattern was determined using BIOLOG EcoPlateTM (Biolog Inc., CA, USA) which contains 31 types of C substrate commonly used by soil microorganisms and one substrate-free control50. For each sample, 10 g fresh soil was placed into a sterilized glass flask to mix with 100 ml of 0.85% sterilized NaCl solution on a reciprocal shaker for 0.5 h and then let stand for 1 h. The supernatant was diluted 1000 times and then 150 μl of the diluted soil suspension were added into each well of the Biolog Eco micro-plate. The micro-plates were incubated for 7 days at 25 oC and optical density was read at 590 nm using a Biolog Gen III Microstation (Biolog Inc., CA, USA) per day to record the color development of soil samples51. Finally, average well color development (AWCD) was calculated to indicate microbial C utilization for each sample. This method can clearly exhibit changes in soil microbial community function to utilize C substrates50 and the results to some extent indicate the similar changes of soil microbial community, e.g, profiled by phospholipid fatty acid analysis52.

The activities of four soil enzymes including cellulase, invertase, urease and catalase were also analyzed to indicate soil microbial community functions10, 53, following the methods proposed by Guan53 and Yao and Huang54. Briefly, soil cellulase and invertase activities were determined by the dinitrosalicylic acid (DNS) reduction and colorimetric method, with 1% carboxymethylcellulose and 8% sucrose solutions as substrates, respectively53, 54. Soils mixed with the according substrate and phosphate buffer solution were incubated at 37 oC for 72 h to analyze soil cellulose activity and for 24 h to analyze soil invertase activity. The DNS solution was then added to develop color for 15 min. Finally, color density was read at 540 and 508 nm to calculate soil cellulase and invertase activity, respectively. Urease activity was analyzed using the phenol-hypochlorite reaction and colorimetric method, with 10% urea solution as a substrate54. After incubated at 37 oC for 24 h, phenol and hypochlorite solutions were added to develop color and then color density was read at 578 nm. Catalase activity was tested by the KMnO4 oxidation and titration method, with 0.3% H2O2 solution as a substrate and 0.02 mol L−1 KMnO4 as an oxidizing reagent53.

Soil available N, P and K contents were determined as described by Bao55. Soil available N was assayed using the alkaline hydrolysis-diffusion method, i.e., the available N was reduced to NH3 at 40 oC for 24 h after adding FeSO4 powder and a NaOH solution and then the NH3 was absorbed using H3BO3 and titrated using H2SO4 to determine soil available N content. Available P content was determined using a spectrophotometer at the wavelength of 700 nm, with 0.05 mol L−1 HCl-0.025 mol L−1 (1/2 H2SO4) as the extractant, ascorbic acid as the reduction agent and a H2SO4-(NH4)6Mo7O24 solution as the color development agent. Soil available K was extracted by 1 mol L−1 NH4OAc solution and K concentration in the extracts was determined by the flame spectrometry method. Soil available N, P and K contents were presented as mg kg−1 soil in this study.

Statistical analyses

Principal component analysis (PCA) was conducted to reveal overall treatment effects on the microbial C utilization pattern originated from BIOLOG analysis. The PCA results could visually present the treatment effects. Moreover, the 31 types of C substrate in BIOLOG EcoPlate were pooled into six groups according to their properties50. For each group of the C substrates, AWCDs were compared between species and among light intensity treatments using independent-samples t test and one-way analysis of variance (ANOVA), respectively. The independent-samples t test and one-way ANOVA were also used to detect significant differences in soil enzyme activities and available N, P and K contents among treatments. Two-way ANOVA was employed to test the main and interactive effects of plant species and light intensity on microbial C utilization pattern, soil enzyme activities or available nutrient contents. For all the statistical analyses, significance level was set at p < 0.05. All these analyses were conducted in IBM SPSS Statistics 22 (IBM Corp., NY, USA) and graphs were made in SigmaPlot 10.0 (Systat Software Inc., CA, USA).

Data availability statement

The datasets generated during the current study are available from the corresponding author on reasonable request.

Electronic supplementary material


This study is financially supported by the Ministry of Education of the People’s Republic of China (20124404110009), Department of Education of Guangdong Province (No. [2013] 246), Guangdong Provincial Department of Science and Technology (2015B090903077), and the National Natural Science Foundation of China (31500401; 31300371).

Author Contributions

Author Contributions

J.Z. and G.Q. designed the experiment. W.Y. and K.L. conducted the study. H.W. conducted data analyses and wrote the initial manuscript. All the authors contributed to data discussion, result explanations and manuscript revisions.


Competing Interests

The authors declare that they have no competing interests.


Electronic supplementary material

Supplementary information accompanies this paper at doi:10.1038/s41598-017-11707-x

Publisher's note: Springer Nature remains neutral with regard to jurisdictional claims in published maps and institutional affiliations.


1. Marris E. The end of the invasion? Nature. 2009;459:327–328. doi: 10.1038/459327a. [Cross Ref]
2. Simberloff D, et al. Impacts of biological invasions: what’s what and the way forward. Trends Ecol. Evol. 2013;28:58–66. doi: 10.1016/j.tree.2012.07.013. [PubMed] [Cross Ref]
3. Castro-Diez P, Godoy O, Alonso A, Gallardo A, Saldana A. What explains variation in the impacts of exotic plant invasions on the nitrogen cycle? A meta-analysis. Ecol. Lett. 2014;17:1–12. doi: 10.1111/ele.12197. [PubMed] [Cross Ref]
4. Callaway RM, Maron JL. What have exotic plant invasions taught us over the past 20 years? Trends Ecol. Evol. 2006;21:369–374. doi: 10.1016/j.tree.2006.04.008. [PubMed] [Cross Ref]
5. Higgins SI, Richardson DM. Invasive plants have broader physiological niches. Proceedings of the National Academy of Sciences of the United States of America. 2014;111:10610–10614. doi: 10.1073/pnas.1406075111. [PubMed] [Cross Ref]
6. Seastedt TR, Pyšek P. Mechanisms of Plant Invasions of North American and European Grasslands. Annu. Rev. Ecol. Evol. S. 2011;42:133–153. doi: 10.1146/annurev-ecolsys-102710-145057. [Cross Ref]
7. Pyšek P, Richardson DM. Invasive Species, Environmental Change and Management, and Health. Annual Review of Environment and Resources. 2010;35:25–55. doi: 10.1146/annurev-environ-033009-095548. [Cross Ref]
8. Coykendall KE, Houseman GR. Lespedeza cuneata invasion alters soils facilitating its own growth. Biological Invasions. 2014;16:1735–1742. doi: 10.1007/s10530-013-0623-8. [Cross Ref]
9. Carey CJ, Beman JM, Eviner VT, Malmstrom CM, Hart SC. Soil microbial community structure is unaltered by plant invasion, vegetation clipping, and nitrogen fertilization in experimental semi-arid grasslands. Front Microbiol. 2015;6:466. doi: 10.3389/fmicb.2015.00466. [PMC free article] [PubMed] [Cross Ref]
10. Sun X, Gao C, Guo L. Changes in soil microbial community and enzyme activity along an exotic plant Eupatorium adenophorum invasion in a Chinese secondary forest. Chinese. Sci. Bull. 2013;58:4101–4108. doi: 10.1007/s11434-013-5955-3. [PubMed] [Cross Ref]
11. Elgersma KJ, Ehrenfeld JG. Linear and non-linear impacts of a non-native plant invasion on soil microbial community structure and function. Biological Invasions. 2010;13:757–768. doi: 10.1007/s10530-010-9866-9. [Cross Ref]
12. Li W, Zhang C, Jiang H, Xin G, Yang Z. Changes in soil microbial community associated with invasion of the exotic weed, Mikania micrantha H.B.K. Plant Soil. 2006;281:309–324. doi: 10.1007/s11104-005-9641-3. [Cross Ref]
13. Hawkes CV, Wren IF, Herman DJ, Firestone MK. Plant invasion alters nitrogen cycling by modifying the soil nitrifying community. Ecol. Lett. 2005;8:976–985. doi: 10.1111/j.1461-0248.2005.00802.x. [Cross Ref]
14. Wang C, Xiao H, Liu J, Wang L, Du D. Insights into ecological effects of invasive plants on soil nitrogen cycles. American Journal of Plant Sciences. 2015;06:34–46. doi: 10.4236/ajps.2015.61005. [Cross Ref]
15. Si, C. C. et al. Different degrees of plant invasion significantly affect the richness of the soil fungal community. Plos One8, (2013). [PMC free article] [PubMed]
16. Wei, H., Xu, J., Quan, G., Zhang, J. & Qin, Z. Effects of Praxelis clematidea invasion on soil nitrogen fractions and transformation rates in a tropical savanna. Environ Sci Pollut Res, doi:10.1007/s11356-016-8127-6 (2016). [PubMed]
17. Liao C, et al. Altered ecosystem carbon and nitrogen cycles by plant invasion: a meta-analysis. New Phytol. 2008;177:706–714. doi: 10.1111/j.1469-8137.2007.02290.x. [PubMed] [Cross Ref]
18. van Kleunen M, Dawson W, Maurel N. Characteristics of successful alien plants. Mol. Ecol. 2015;24:1954–1968. doi: 10.1111/mec.13013. [PubMed] [Cross Ref]
19. Fierer N, Bradford MA, Jackson RB. Toward an ecological classification of soil bacteria. Ecology. 2007;88:1354–1364. doi: 10.1890/05-1839. [PubMed] [Cross Ref]
20. Hogberg MN, Hogberg P, Myrold DD. Is microbial community composition in boreal forest soils determined by pH, C-to-N ratio, the trees, or all three? Oecologia. 2007;150:590–601. doi: 10.1007/s00442-006-0562-5. [PubMed] [Cross Ref]
21. Wei H, et al. Thermal acclimation of organic matter decomposition in an artificial forest soil is related to shifts in microbial community structure. Soil Biol. Biochem. 2014;71:1–12. doi: 10.1016/j.soilbio.2014.01.003. [Cross Ref]
22. Qin Z, et al. Impacts of the invasive annual herb Ambrosia artemisiifolia L. on soil microbial carbon source utilization and enzymatic activities. Eur. J. Soil Biol. 2014;60:58–66. doi: 10.1016/j.ejsobi.2013.11.007. [Cross Ref]
23. Inderjit & van der Putten, W. H. Impacts of soil microbial communities on exotic plant invasions. Trends Ecol. Evol. 25, 512-519, doi: 10.1016/j.tree.2010.06.006 (2010). [PubMed]
24. Cui QG, He WM. Soil biota, but not soil nutrients, facilitate the invasion of Bidens pilosa relative to a native species Saussurea deltoidea. Weed Res. 2009;49:201–206. doi: 10.1111/j.1365-3180.2008.00679.x. [Cross Ref]
25. Yue M, et al. Effects of extreme temperatures on the growth and photosynthesis of invasive Bidens alba and its native congener B. biternata. Nord. J. Bot. 2017;35:377–384. doi: 10.1111/njb.01365. [Cross Ref]
26. Siemann E, Rogers WE. Changes in light and nitrogen availability under pioneer trees may indirectly facilitate tree invasions of grasslands. J. Ecol. 2003;91:923–931. doi: 10.1046/j.1365-2745.2003.00822.x. [Cross Ref]
27. Young SL, Kyser GB, Barney JN, Claassen VP, DiTomaso JM. The role of light and soil moisture in plant community resistance to invasion by Yellow starthistle (Centaurea solstitialis) Restor. Ecol. 2011;19:599–606. doi: 10.1111/j.1526-100X.2010.00686.x. [Cross Ref]
28. Porte AJ, Lamarque LJ, Lortie CJ, Michalet R, Delzon S. Invasive Acer negundo outperforms native species in non-limiting resource environments due to its higher phenotypic plasticity. BMC Ecology. 2011;11:28. doi: 10.1186/1472-6785-11-28. [PMC free article] [PubMed] [Cross Ref]
29. Maurer D, Zedler J. Differential invasion of a wetland grass explained by tests of nutrients and light availability on establishment and clonal growth. Oecologia. 2002;131:279–288. doi: 10.1007/s00442-002-0886-8. [PubMed] [Cross Ref]
30. van Kleunen M, Schlaepfer DR, Glaettli M, Fischer M. Preadapted for invasiveness: do species traits or their plastic response to shading differ between invasive and non-invasive plant species in their native range? J. Biogeogr. 2011;38:1294–1304. doi: 10.1111/j.1365-2699.2011.02495.x. [Cross Ref]
31. Pattison RR, Goldstein G, Ares A. Growth, biomass allocation and photosynthesis of invasive and native Hawaiian rainforest species. Oecologia. 1998;117:449–459. doi: 10.1007/s004420050680. [PubMed] [Cross Ref]
32. Zhang K-M, et al. Photosynthetic electron-transfer reactions in the gametophyte of Pteris multifida reveal the presence of allelopathic interference from the invasive plant species Bidens pilosa. Journal of Photochemistry and Photobiology B: Biology. 2016;158:81–88. doi: 10.1016/j.jphotobiol.2016.02.026. [PubMed] [Cross Ref]
33. Khanh TD, et al. Allelopathic plants: 20. Hairy Beggarticks (Bidens pilosa L.) Allelopathy Journal. 2009;24:243–254.
34. Wang R, et al. Effects of simulated acid rain on seedling growth and allelopathic potential of invasive alien species Bidens pilosa L. Ecology and Environment. 2010;19:2845–2849.
35. Hsu H-M, Kao W-Y. Vegetative and reproductive growth of an invasive weed Bidens pilosa L. var. radiata and its noninvasive congener Bidens bipinnata in Taiwan. Taiwania. 2014;59:119–126.
36. Sîrbu C, Oprea A. New alien species for the flora of Romania: Bidens bipinnata L. (Asteraceae) Turkish Journal of Botany. 2008;32:255–258.
37. Yuan LP, et al. Protective effects of total flavonoids of Bidens bipinnata L. against carbon tetrachloride-induced liver fibrosis in rats. J. Pharm. Pharmacol. 2008;60:1393–1402. doi: 10.1211/jpp.60.10.0016. [PubMed] [Cross Ref]
38. Fenner M. The inhibition of germination of Bidens pilosa seeds by leaf canopy shade in some natural vegetation types. New Phytol. 1980;84:95–101. doi: 10.1111/j.1469-8137.1980.tb00751.x. [Cross Ref]
39. He B, et al. Effects of Bidens pilosa of invasion plant on soil ecological system at different developmental stages. Southwest China Journal of Agricultural Sciences. 2013;26:1953–1956.
40. Vila M, et al. Ecological impacts of invasive alien plants: a meta-analysis of their effects on species, communities and ecosystems. Ecol. Lett. 2011;14:702–708. doi: 10.1111/j.1461-0248.2011.01628.x. [PubMed] [Cross Ref]
41. Ehrenfeld JG. Effects of exotic plant invasions on soil nutrient cycling processes. Ecosystems. 2003;6:503–523. doi: 10.1007/s10021-002-0151-3. [Cross Ref]
42. Allison SD, Nielsen C, Hughes RF. Elevated enzyme activities in soils under the invasive nitrogen-fixing tree Falcataria moluccana. Soil Biol. Biochem. 2006;38:1537–1544. doi: 10.1016/j.soilbio.2005.11.008. [Cross Ref]
43. Marschner P, Umar S, Baumann K. The microbial community composition changes rapidly in the early stages of decomposition of wheat residue. Soil Biol. Biochem. 2011;43:445–451. doi: 10.1016/j.soilbio.2010.11.015. [Cross Ref]
44. Evans JR. Nitrogen and photosynthesis in the flag leaf of wheat (Triticum aestivum L.) Plant Physiol. 1983;72:297–302. doi: 10.1104/pp.72.2.297. [PubMed] [Cross Ref]
45. Wilson D, Cooper JP. Effects of light intensity and CO2 on apparent photosynthesis and its relationship with leaf anatomy in genotypes of Lolium perenne L. New Phytol. 1969;68:627–644. doi: 10.1111/j.1469-8137.1969.tb06467.x. [Cross Ref]
46. Hu J, Yang H, Long X, Liu Z, Rengel Z. Pepino (Solanum muricatum) planting increased diversity and abundance of bacterial communities in karst area. Scientific Reports. 2016;6:21938. doi: 10.1038/srep21938. [PMC free article] [PubMed] [Cross Ref]
47. Schachtman DP, Reid RJ, Ayling SM. Phosphorus uptake by plants: from soil to cell. Plant Physiol. 1998;116:447–453. doi: 10.1104/pp.116.2.447. [PubMed] [Cross Ref]
48. Römheld V, Kirkby EA. Research on potassium in agriculture: needs and prospects. Plant Soil. 2010;335:155–180. doi: 10.1007/s11104-010-0520-1. [Cross Ref]
49. Cao Y, Wang S, Zhang G, Luo J, Lu S. Chemical characteristics of wet precipitation at an urban site of Guangzhou, South China. Atmos. Res. 2009;94:462–469. doi: 10.1016/j.atmosres.2009.07.004. [Cross Ref]
50. Choi K-H, Dobbs FC. Comparison of two kinds of Biolog microplates (GN and ECO) in their ability to distinguish among aquatic microbial communities. J. Microbiol. Meth. 1999;36:203–213. doi: 10.1016/S0167-7012(99)00034-2. [PubMed] [Cross Ref]
51. Xu HQ, et al. Effects of simulated acid rain on microbial characteristics in a lateritic red soil. Environ. Sci. Pollut. R. 2015;22:18260–18266. doi: 10.1007/s11356-015-5066-6. [PubMed] [Cross Ref]
52. Grayston SJ, et al. Assessing shifts in microbial community structure across a range of grasslands of differing management intensity using CLPP, PLFA and community DNA techniques. Appl. Soil Ecol. 2004;25:63–84. doi: 10.1016/S0929-1393(03)00098-2. [Cross Ref]
53. Guan, S. Soil enzymes and the analytical methods. (China Agriculture Press, 1986).
54. Yao, H. & Huang, C. Soil microbial ecology and the related experimental techniques. (Science Press Ltd., 2007).
55. Bao, S. Agro-Chemical analyses of soils. (China Agruculture Press, 2000).

Articles from Scientific Reports are provided here courtesy of Nature Publishing Group