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Article

Does Bidens pilosa L. Affect Carbon and Nitrogen Contents, Enzymatic Activities, and Bacterial Communities in Soil Treated with Different Forms of Nitrogen Deposition?

by
Yingsheng Liu
1,
Yizhuo Du
1,
Yue Li
1,
Chuang Li
1,
Shanshan Zhong
1,
Zhelun Xu
1,2,
Congyan Wang
1,3,* and
Daolin Du
4,*
1
School of Environment and Safety Engineering, Jiangsu University, Zhenjiang 212013, China
2
Weed Research Laboratory, College of Life Sciences, Nanjing Agricultural University, Nanjing 210095, China
3
Jiangsu Collaborative Innovation Center of Technology and Material of Water Treatment, Suzhou University of Science and Technology, Suzhou 215009, China
4
Jingjiang College, Jiangsu University, Zhenjiang 212013, China
*
Authors to whom correspondence should be addressed.
Microorganisms 2024, 12(8), 1624; https://doi.org/10.3390/microorganisms12081624
Submission received: 13 July 2024 / Revised: 7 August 2024 / Accepted: 8 August 2024 / Published: 9 August 2024
(This article belongs to the Special Issue Rhizosphere Bacteria and Fungi that Promote Plant Growth)
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Abstract

:
The deposition of nitrogen in soil may be influenced by the presence of different nitrogen components, which may affect the accessibility of soil nitrogen and invasive plant–soil microbe interactions. This, in turn, may alter the success of invasive plants. This study aimed to clarify the influences of the invasive plant Bidens pilosa L. on the physicochemical properties, carbon and nitrogen contents, enzymatic activities, and bacterial communities in soil in comparison to the native plant Pterocypsela laciniata (Houtt.) Shih treated with simulated nitrogen deposition at 5 g nitrogen m−2 yr−1 in four forms (nitrate, ammonium, urea, and mixed nitrogen). Monocultural B. pilosa resulted in a notable increase in soil pH but a substantial decrease in the moisture, electrical conductivity, ammonium content, and the activities of polyphenol oxidase, β-xylosidase, FDA hydrolase, and sucrase in soil in comparison to the control. Co-cultivating B. pilosa and P. laciniata resulted in a notable increase in total soil organic carbon content in comparison to the control. Monocultural B. pilosa resulted in a notable decrease in soil bacterial alpha diversity in comparison to monocultural P. laciniata. Soil FDA hydrolase activity and soil bacterial alpha diversity, especially the indices of Shannon’s diversity, Simpson’s dominance, and Pielou’s evenness, exhibited a notable decline under co-cultivated B. pilosa and P. laciniata treated with nitrate in comparison to those treated with ammonium, urea, and mixed nitrogen.

1. Introduction

Invasive plants (IPs) have the potential to exert a considerable influence on environmental health and ecological security. In particular, IPs can affect the ecological functioning of native ecosystems, which can result in a loss of native biodiversity [1,2,3,4]. At present, there are in excess of 500 IPs distributed throughout China [5]. This is primarily attributable to the considerable diversity of habitats and climates, in addition to the recent surge in human activities, especially international trade, in China [5]. Furthermore, the Asteraceae family is the most species-rich among IPs in China, with 92 documented species to date. It constitutes ~17.86% of the total species number within IPs in China [5]. It is, therefore, crucial to elucidate the primary mechanisms underlying the successful establishment of IPS, with a particular emphasis on those observed in the Asteraceae family, as this represents a pivotal area of research within the field of invasion ecology [1,4,6,7].
One of the primary reasons for the successful colonization of IPs is their capacity to create soil microenvironments that are more conducive to further invasion through the formation of mutualistic interactions with soil microorganisms. This is accomplished through the release of a multitude of nutrients resulting from growth metabolism, litter decomposition, and root secretion, in addition to other processes. This, in turn, affects the cycling of soil nutrients, including carbon (C) and nitrogen (N), and alters the metabolic activity and community structure of soil microorganisms, thus facilitating the invasion process [8,9,10,11]. It is, therefore, of great importance to elucidate the key mechanisms by which IPS, especially the Asteraceae IPS, are successfully colonized via mutualistic interactions with soil microorganisms.
In general, N is one of the key nutritional components that restricts plant growth in several terrestrial ecosystems [12,13,14,15]. Consequently, the capacity of IPs to procure N is a pivotal determinant of their success in colonizing a diverse array of habitats. In particular, IPs are more proficient at acquiring N than native plants due to their superior levels of N availability and utilization [16,17,18,19]. Moreover, the invasion intensity and invasiveness of numerous IPs are also strongly correlated with soil N availability [20,21,22,23]. Furthermore, the invasibility of plant communities is also strictly linked to the accessibility of soil N [24,25,26]. However, the accessibility of soil N and invasive plant–soil microbe interactions may be significantly altered by atmospheric N deposition, which in turn may affect the colonization process of IPs.
The level of atmospheric N deposition has continued to increase in recent years, primarily due to the release of nitrogen-containing substances into the atmosphere from the combustion of fossil fuels in excess, the irrational or improper creation and use of nitrogenous fertilizers, the speedy progress of livestock and farming, etc. [27,28,29,30]. Presently, East Asia (principally China) has one of the three maximum levels of N deposition globally [28,31,32,33]. Nevertheless, it has been demonstrated that excessive N deposition can result in soil acidification, disturb plant growth, decrease species diversity, and significantly interrupt the ecological health and balance of ecosystems [34,35,36,37]. Moreover, N deposition can facilitate the invasion intensity and invasiveness of numerous IPs, thereby facilitating their colonization process [38,39,40,41]. It is essential to recognize that N deposition encompasses a diverse range of N components, including but not limited to NH4-N, NO3-N, and CO(NH2)2-N. The relative proportions of these components are subject to fluctuations as a consequence of alterations in energy policies and the energy mix used [42,43,44,45]. However, the deposition of N in different forms may modify the accessibility of N in soil and the interactions between IPs and soil microorganisms, which may, in turn, affect the colonization process of IPs. It is, therefore, imperative to survey the effects of N deposition with distinct N components on the available level of N in soil and the interactions between IPs and soil microorganisms. The objective of this examination is to explicate the mechanisms that facilitate the successful colonization of IPs treated with N deposition, with a particular focus on the effects of different forms of N components.
This study aimed to explicate the impacts of the Asteraceae IPs Bidens pilosa L. on the physicochemical properties, C and N contents, enzymatic activities, and the structure of the bacterial communities in soil (SBC) in comparison to those of the Asteraceae native plant Pterocypsela laciniata (Houtt.) Shih. This study was conducted with simulated N deposition at 5 g N m−2 yr−1 in four forms (nitrate (NO3-N), ammonium (NH4-N), urea (CO(NH2)2-N), and a mixed N solution comprising an equal mixture of the three individual N forms). This study was carried out over a four-month period using a pot cultivation experiment. Bidens pilosa has its origins in the tropical Americas and was presented to China in 1857 as part of a shipment of imported crops and vegetables. Nevertheless, B. pilosa has been identified as a significant threat to ecosystem structure and function, particularly in terms of biodiversity loss in China. Additionally, B. pilosa has been designated as a significant IP in China [4,46,47,48]. Moreover, the geographic distribution of the two Asteraceae species observed in China is among the most affected by N deposition [28,31,32,33].
The following hypotheses were proposed for this study: (1) B. pilosa may demonstrate a more pronounced increase in C and N contents, enzymatic activities in soil, and SBC’s alpha diversity in comparison to P. laciniata. (2) N form is a pivotal factor influencing C and N contents, enzymatic activities in soil, SBC’s alpha diversity, and SBC’s structure.

2. Materials and Methods

2.1. Experimental Design

The target IP was identified as B. pilosa. Pterocypsela laciniata was selected as the native species. Seeds of B. pilosa and P. laciniata were collected from Zhenjiang (32.15–32.16° N; 119.52–119.53° E), Jiangsu, China, in October 2022. Figure S1 provides a map indicating the geographical location of the sampled zone in this study.
A pot cultivation experiment was carried out to examine the growth of B. pilosa and P. laciniata. Pasture yellow soil (manufacturer: Shenzhibei Sci. & Technol. Co., Ltd., Baishan, China; pH value: ~6.3; organic content: ≥30%; soil electrical conductivity: ≤3 ms/cm; ~3 kg/planting basin) was selected as the culture substrate. The rationale behind the utilization of pasture yellow soil was twofold: firstly, to minimize the possibility of IPs having been introduced previously, and secondly, to mitigate the risk of contamination from N deposition in the natural soil. Seeds of B. pilosa and P. laciniata were located in garden pots (top diameter 25 cm; height 16.5 cm). A total of six seedlings of B. pilosa and/or P. laciniata with uniform size and robust growth were placed in each garden pot. The treatments were as follows: (1) six seedlings of B. pilosa per garden pot (monocultural B. pilosa (BP)); (2) three seedlings of B. pilosa and P. laciniata per garden pot (co-cultivated B. pilosa and P. laciniata (BPPL)); and (3) six seedlings of P. laciniata per garden pot (monocultural P. laciniata (PL)). All garden pots were treated with simulated N deposition comprising four forms: (1) nitrate (potassium nitrate (KNO3, AR, ≥99%; Aladdin®, Shanghai, China); inorganic nitrogen); (2) ammonium (ammonium chloride (NH4Cl, GR, ≥99.8%; Sinopharm Chemical Reagent Co., Ltd., Shanghai, China); inorganic nitrogen); (3) urea (CO(NH2)2, BC, ≥99.5%; Sangon Biotech Co., Ltd., Shanghai, China; organic nitrogen); (4) mixed N (nitrate–ammonium–urea = 1:1:1), at 5 g N m−2 yr−1. Sterile distilled water was employed as the control treatment, with a N concentration of 0 g N L−1. The content of simulated N deposition in the four aforementioned forms was set to match the real content (i.e., 5 g N m−2 yr−1) of the natural N deposition in southern Jiangsu, China, as documented in previous studies [31,32,49,50]. The proportion of three individual N in mixed N was approximated to the actual proportion of natural N deposition in southern Jiangsu, China, as documented in references [42,43,51]. All possible combinations of planted types (i.e., BP, BPPL, and PL) and N forms (i.e., nitrate, ammonium, urea, and mixed N) were investigated in this present study. Three replicates were scheduled for each treatment. The seedlings of B. pilosa and P. laciniata were cultivated in a greenhouse at Zhenjiang (32.2061° N, 119.5128° E), Jiangsu, China, under natural light for ~4 months from April to July 2023.
After a period of ~4 months, three soil cores were extracted from a depth of ~2 cm around the roots of the two plant species per garden pot via the root shaking method. Subsequently, the soil cores were homogenized to create a single soil sample, with three replicates per treatment. Soil samples were screened via a 2 mm sieve to remove any impurities, thus allowing the measurement of soil physicochemical properties, soil C and N contents, soil enzymatic activities, and SBC’s structure.

2.2. Determination of Soil Physicochemical Properties and Soil C and N Contents

The pH, moisture, and electrical conductivity in soil were analyzed in situ via the digital meters to ascertain soil acidity (LY-601; Jiaheng Instrument Co., Ltd., Qingdao, China) and electrical conductivity (EC-8801A; Hetai Instrument Co., Ltd., Huai’an, China).
Total soil organic C and N contents, as well as soil microbial C and N contents, were all analyzed using the chloroform fumigation method [52,53]. In particular, total soil organic C and N were extracted with 0.5 mol L−1 K2SO4 (1:4 soil–solution) before and after a 24 h period of chloroform fumigation. The extractable organic C and N contents in the soil extracts were subsequently analyzed by using the TOC analyzer (Analytik Jena, Jena, Germany) and flow injection analyzer (Zellwegger Analytical, Milwaukee, WI, USA), respectively. Soil microbial C and N contents were calculated as the difference between the extractable organic C and N contents of non-fumigated and fumigated soils, and an efficiency factor of 0.45 was employed to correct for incomplete extraction [52,53,54,55].
Soil ammonium and nitrate contents were analyzed by using the potassium chloride leaching method in accordance with the national standard of China (GB/T 42485-2023) [56]. In particular, soil ammonium and nitrate were extracted with 1 mol L−1 KCl (1:5 soil–solution) over a period of 1 h. The extractable ammonium and nitrate contents in the soil extracts were then analyzed spectrophotometrically at 543 nm and 630 nm, respectively.

2.3. Determination of Soil Enzymatic Activities

Several soil enzymatic activities were investigated, with a particular focus on those that affect soil C and N cycling. The following methods were employed: soil polyphenol oxidase activity was determined via the Assay Kit of Polyphenol Oxidase Activity (No.: D799508-0100; spectrophotometrically at 430 nm); soil cellulase activity was determined via the Assay Kit of Soil Cellulase Activity (No.: D799514-0100; spectrophotometrically at 540 nm); soil β-glucosidase activity was determined via the Assay Kit of Soil β-glucosidase Activity (No.: D799510-0100; spectrophotometrically at 400 nm); soil β-xylosidase activity was determined via the Assay Kit of Soil β-xylosidase Activity (No.: D799556-0100; spectrophotometrically at 400 nm); soil FDA hydrolase activity was determined via the Assay Kit of Soil FDA Hydrolase Activity (No.: D799552-0100; spectrophotometrically at 490 nm); soil sucrase activity was determined via the Assay Kit of Soil Sucrase Activity (No.: D799504-0100; spectrophotometrically at 540 nm); soil protease activity was determined via the Assay Kit of Soil Protease Activity (No.: D799540-0100; spectrophotometrically at 680 nm); soil urease activity was determined via the Assay Kit of Soil Urease Activity (No.: D799506-0100; spectrophotometrically at 630 nm) (Sangon Biotech Co., Ltd., Shanghai, China) with micromethod.

2.4. Determination of SBC’s Structure

To ascertain SBC’s structure, each soil sample was subjected to individual processing. The total DNA from all soil samples was extracted using the HiPure Soil DNA Kits (Magen, Guangzhou, China). The integrity of the total DNA was ascertained through electrophoresis on 1.2% (weight–volume) agarose gels. The quantity of DNA was determined by using the ABI StepOnePlus Real-Time PCR System (Life Technologies, Foster City, CA, USA).
The amplification of the V3–V4 region of the 16S rRNA genes of SBC was conducted via the universal primers (341F and 806R) as previously described [57,58]. The amplicons were extracted from 2% (weight–volume) agarose gels and purified by using the AxyPrep DNA Gel Extraction Kit (Axygen Biosciences, Union City, CA, USA) in accordance with the manufacturer’s instructions and then quantified by using the ABI StepOnePlus Real-Time PCR System (Life Technologies, Foster City, CA, USA). The purified amplicons were pooled in equimolar amounts and subjected to paired-end sequencing on the Illumina platform at GENE DENOVO Co., Ltd., Guangzhou, Guangdong, China, in accordance with the standard protocols.
The raw data containing adapters or low-quality reads would affect the following assembly and analysis. Thus, to obtain high-quality clean reads, the raw reads were further filtered according to the following rules by using FASTP v0.18.0: (1) Removing reads containing more than 10% of unknown nucleotides (N); (2) Removing reads containing less than 50% of bases with a quality (Q-value) > 20. The paired-end clean reads were merged as raw tags using FLASH v1.2.11 with a minimum overlap of 10 bp and mismatch error rates of 2%. The noisy sequences of the raw tags were filtered under specific filtering conditions to obtain high-quality, clean tags. The filtering conditions are as follows: (1) The break raw tags from the first low-quality base site where the number of bases in the continuous low-quality value (the default quality threshold is ≤3) reaches the set length (the default length is 3 bp); (2) The filter tags whose continuous high-quality base length is less than 75% of the tag length.
The clean tags were clustered into operational taxonomic units (OTUs) of ≥97% similarity using the UPARSE v9.2.64 pipeline. All chimeric tags were removed using the UCHIME algorithm, and we finally obtained effective tags for further analysis. The tag sequence with the highest abundance was selected as a representative sequence within each cluster. The representative OTU sequences or ASV sequences were classified into organisms by a naïve Bayesian model using the RDP classifier v2.2 based on the SILVA database v138.1, with a confidence threshold value of 0.8.
The abundance statistics of each taxonomy were visualized using Krona v2.6. The stacked bar plot of the community composition was visualized in the R project ggplot2 package v2.2.1. The circular layout representations of species abundance were graphed using Circos v0.69-3. The heatmap of species abundance was plotted by using the p-heatmap package v1.0.12 in the R project. The Pearson correlation analysis of species was calculated in the R project psych package v1.8.4. The OTU’s species index, Shannon’s diversity index, Simpson’s dominance index, Pielou’s evenness index, Chao1’s richness index, and ACE’s richness index were calculated in QIIME v1.9.1. The phylogenetic diversity index was calculated in Picante v1.8.2.
The sequence alignment was performed using Muscle v3.8.31, and the phylogenetic tree was constructed using FastTree v2.1, then weighted and unweighted unifrac distance matrices were generated using GuniFrac package v1.0 in the R project. Jaccard and Bray–Curtis distance matrix calculated in the R project Vegan package v2.5.3. The biomarker features in each group were screened using the LEfSe software v1.0. The multivariate statistical techniques, including PCoA (principal coordinates analysis) and NMDS (non-metric multi-dimensional scaling) of (Un) weighted unifrac, jaccard, and Bray–Curtis distances, were generated in the R project Vegan package v2.5.3 and plotted in the R project ggplot2 package v2.2.1.

2.5. Statistical Analysis

The normality and homogeneity of the determined variances were evaluated through the application of Shapiro–Wilk’s test and Bartlett’s test, respectively. A multiple comparison test was employed to analyze the statistical differences in the values of the physicochemical properties, C and N contents, enzymatic activities in soil, and SBC’s alpha diversity among the different treatments via the Tukey test. A two-way ANOVA was employed to assess the impacts of planted type and N form on the physicochemical properties, C and N contents, enzymatic activities in soil, and SBC’s alpha diversity. The effect size of each factor was also evaluated by using the Partial Eta Squared (η2) values, which were designed to inform the two-way ANOVA. Correlation patterns of soil physicochemical properties, soil C and N contents, soil enzymatic activities, and SBC’s alpha diversity were estimated using correlation analysis and principal component analysis (PCA). The threshold for statistical significance was set at p ≤ 0.05. Statistical analyses were conducted using IBM SPSS Statistics 26.0 (IBM, Inc., Armonk, NY, USA).

3. Results

3.1. The Influences of Planted Type

3.1.1. Soil Physicochemical Properties

The soil pH under PL and BP was higher than that under the control (p < 0.05; Figure 1a). Soil pH under BP was also greater than that under BPPL (p < 0.05; Figure 1a). Soil pH under BP and BPPL was larger than that under PL treated with all forms of N (p < 0.05; Figure 1a).
Soil moisture under BP was less than that under the control, PL, and BPPL (p < 0.05; Figure 1b). Soil moisture under BP and BPPL was less than that under PL treated with nitrate and ammonium (p < 0.05; Figure 1b). Soil moisture under BP was lower than that under PL and BPPL treated with urea and mixed N (p < 0.05; Figure 1b).
Soil electrical conductivity under BP was lower than that under the control (p < 0.05; Figure 1c). Soil electrical conductivity under BP and BPPL was lower than that under PL treated with urea (p < 0.05; Figure 1c). Soil electrical conductivity under BP was less than that under PL treated with mixed N (p < 0.05; Figure 1c).
According to the two-way ANOVA analysis, planted type significantly affected soil pH, soil moisture, and soil electrical conductivity (p < 0.001; Table S1).

3.1.2. Soil C and N Contents

Total soil organic C content under BPPL was higher than that under the control and BP (p < 0.05; Figure 2a).
Soil ammonium content under BP was lower than that under the control and BPPL (p < 0.05; Figure 2b). Soil ammonium content under BPPL was higher than that under PL and BP treated with nitrate, ammonium, and urea (p < 0.05; Figure 2b).
According to the two-way ANOVA analysis, planted type significantly affected soil ammonium content (p < 0.001; Table S1).

3.1.3. Soil Enzymatic Activities

Soil polyphenol oxidase activity under PL, BP, and BPPL was less than that under the control (p < 0.05; Figure 3a).
Soil β-xylosidase activity under BP was lower than that under the control (p < 0.05; Figure 3d).
Soil FDA hydrolase activity under BP and BPPL was lower than that under the control and PL (p < 0.05; Figure 3e). Soil FDA hydrolase activity under BPPL was less than that under PL treated with nitrate (p < 0.05; Figure 3e). Soil FDA hydrolase activity under BP and BPPL was less than that under PL treated with ammonium, urea, and mixed N (p < 0.05; Figure 3e).
Soil sucrase activity under BP and BPPL was less than that under the control (p < 0.05; Figure 3f).
Soil protease activity under BP and BPPL was lower than that under PL treated with urea (p < 0.05; Figure 3g).
Soil urease activity under BP was lower than that under PL (p < 0.05; Figure 3h). Soil urease activity under BP and BPPL was lower than that under PL treated with nitrate and urea (p < 0.05; Figure 3h). Soil urease activity under BPPL was lower than that under PL treated with mixed N (p < 0.05; Figure 3h).
According to the two-way ANOVA analysis, planted type significantly affected polyphenol oxidase activity, β-xylosidase activity, FDA hydrolase activity, sucrase activity, protease activity, and urease activity in soil (p < 0.05; Table S1).

3.1.4. SBC’s Alpha Diversity

The OTU’s species index under PL was larger than that under the control and BP (p < 0.05; Figure 4a). The OTU’s species index under BP and BPPL was less than that under PL treated with nitrate and ammonium (p < 0.05; Figure 4a). The OTU’s species index under BP was less than that under PL treated with mixed N (p < 0.05; Figure 4a).
The Shannon’s diversity index under BP was less than that under PL (p < 0.05; Figure 4b). The Shannon’s diversity index under BP was also lower than that under PL treated with nitrate, ammonium, and mixed N (p < 0.05; Figure 4b).
The Simpson’s dominance index under BPPL was less than that under PL treated with nitrate (p < 0.05; Figure 4c).
The Pielou’s evenness index under BP was less than that under PL (p < 0.05; Figure 4d). The Pielou’s evenness index under BP and BPPL was less than that under PL treated with nitrate (p < 0.05; Figure 4d). The Pielou’s evenness index under BP was less than that under PL treated with ammonium and mixed N (p < 0.05; Figure 4d).
The Chao1’s richness index and ACE’s richness index under PL were larger than those under the control and BP (p < 0.05; Figure 4e,f). The Chao1’s richness index and ACE’s richness index under BP and BPPL were lower than those under PL treated with nitrate and ammonium (p < 0.05; Figure 4e,f). The Chao1’s richness index and ACE’s richness index under BP were lower than those under PL treated with mixed N (p < 0.05; Figure 4e,f).
The phylogenetic diversity index under BP was lower than that under PL (p < 0.05; Figure 4g). The phylogenetic diversity index under BP and BPPL was lower than that under PL treated with all forms of N (p < 0.05; Figure 4g).
According to the results of the two-way ANOVA analysis, planted type significantly affected all SBC’s alpha diversity indices (except the Simpson’s dominance index) (p < 0.05; Table S1).

3.2. The Influences of N Form

3.2.1. Soil Physicochemical Properties

Soil pH under PL treated with ammonium and mixed N was less than that under PL (p < 0.05; Figure 1a). Soil pH under PL treated with mixed N was also less than that under PL treated with urea (p < 0.05; Figure 1a). The soil pH under BPPL treated with nitrate, urea, and mixed N was greater than that under BPPL (p < 0.05; Figure 1a).
Soil moisture under BP treated with urea was less than that under BP and BP treated with nitrate, ammonium, and mixed N (p < 0.05; Figure 1b). Soil moisture under BPPL treated with nitrate, ammonium, and urea was lower than that under BPPL (p < 0.05; Figure 1b). Soil moisture under BPPL treated with nitrate and ammonium was also lower than that under BPPL treated with mixed N (p < 0.05; Figure 1b). Similarly, soil moisture under BPPL treated with nitrate was less than that under BPPL treated with urea (p < 0.05; Figure 1b).
Soil electrical conductivity under BP treated with urea was greater than that under BP treated with nitrate (p < 0.05; Figure 1c).
According to the two-way ANOVA analysis, N form significantly impacted soil pH and moisture (p < 0.05; Table S1).

3.2.2. Soil C and N Contents

Soil nitrate content under BP treated with urea and mixed N was lower than that under BP (p < 0.05; Figure 2b).
Soil ammonium content under BP treated with urea was greater than that under BP (p < 0.05; Figure 2c). Soil ammonium content under BPPL treated with nitrate, ammonium, and urea was larger than that under BPPL (p < 0.05; Figure 2c). Soil ammonium content under BPPL treated with nitrate was also larger than that under BPPL treated with mixed N (p < 0.05; Figure 2c).
Based on the results of the two-way ANOVA analysis, N form significantly affected soil ammonium content (p < 0.01; Table S1).

3.2.3. Soil Enzymatic Activities

Soil polyphenol oxidase activity under BP treated with ammonium was larger than that under BP treated with mixed N (p < 0.05; Figure 3a). Soil β-glucosidase activity under BP treated with nitrate was larger than that under BP treated with urea (p < 0.05; Figure 3c).
Soil FDA hydrolase activity under PL treated with nitrate was less than that under PL and PL treated with ammonium, urea, and mixed N (p < 0.05; Figure 3e).
Soil protease activity under PL treated with urea was lower than that under PL and PL treated with nitrate, ammonium, and mixed N (p < 0.05; Figure 3g).
Soil urease activity under PL treated with urea was larger than that under PL treated with nitrate and ammonium (p < 0.05; Figure 3h).
According to the two-way ANOVA analysis, N form significantly impacted soil protease activity (p < 0.01; Table S1).

3.2.4. SBC’s Alpha Diversity

The OTU’s species index and Simpson’s dominance index under BPPL treated with nitrate were lower than those under BPPL (p < 0.05; Figure 4a,c).
The Shannon’s diversity index and Pielou’s evenness index under BPPL treated with nitrate were lower than those under BPPL and BPPL treated with ammonium, urea, and mixed N (p < 0.05; Figure 4b,d).
The Chao1’s richness index, ACE’s richness index, and phylogenetic diversity index under BPPL treated with nitrate were less than those under BPPL (p < 0.05; Figure 4e–g).
According to the two-way ANOVA analysis, N form significantly affected Simpson’s dominance index, Pielou’s evenness index, and Chao1’s richness index (p < 0.01; Table S1).

3.3. Correlation Patterns of the Physicochemical Properties, C and N Contents, and Enzymatic Activities in Soil, and SBC’s Alpha Diversity

According to the correlation analysis, soil pH and soil microbial C content were significantly negatively correlated with all indices of SBC’s alpha diversity (p < 0.05; Table S2). Similarly, soil ammonium content was significantly negatively correlated with the phylogenetic diversity index (p < 0.05; Table S2). Soil moisture and soil electrical conductivity were significantly positively correlated with all indices of SBC’s alpha diversity (p < 0.05; Table S2). In addition, soil FDA hydrolase activity and soil urease activity were significantly positively correlated with all indices of SBC’s alpha diversity except Simpson’s dominance index (p < 0.05; Table S2). Soil β-xylosidase activity and soil sucrase activity were also significantly positively correlated with Pielou’s evenness index (p < 0.05; Table S2).
Strong correlations were observed between SBC’s alpha diversity and moisture, electrical conductivity, FDA hydrolase activity, protease activity, and urease activity in soil (Figure 5).

3.4. SBC’s Structure

The mean of the Good’s coverage index across all samples was ~0.9772. The SBC’s beta diversity treated with different planted types and N forms presented noticeable differences according to the weighted UniFrac distances (Figures S2–S4).
The leading role of the principal SBC’s biomarkers, Parcubacteria, Anaerolineae, and Saccharimonadia, was notably improved under PL compared to the control. The leading role of the principal SBC’s biomarkers, Blastocatellia, Saccharimonadia, and Cyanobacteriia, was notably improved under PL treated with nitrate compared to PL. The leading role of the principal SBC’s biomarkers, Chloroflexia and Saccharimonadia, was notably improved under PL treated with ammonium compared to PL. The leading role of the principal SBC’s biomarkers, Parcubacteria, Gammaproteobacteria, Saccharimonadia, and Bacteroidia, was notably improved under PL treated with urea compared to PL. The leading role of the principal SBC’s biomarkers, Parcubacteria and Saccharimonadia, was notably improved under PL treated with mixed N compared to PL (Figure S5a).
The leading role of the principal SBC’s biomarkers, Blastocatellia, Saccharimonadia, Cyanobacteriia, and Alphaproteobacteria, was notably improved under BP compared to the control. The leading role of the principal SBC’s biomarker, Saccharimonadia, was notably improved under BP treated with all forms of N compared to BP (Figure S5b).
The leading role of the principal SBC’s biomarkers, Parcubacteria and Saccharimonadia, was notably improved under BPPL compared to the control. The leading role of the principal SBC’s biomarkers, Chloroflexia and Saccharimonadia, was notably improved under BPPL treated with nitrate compared to BPPL. The leading role of the principal SBC’s biomarker, Saccharimonadia, was notably improved under BPPL treated with ammonium, urea, and mixed N compared to BPPL (Figure S5c).
Based on the results of the LEfSe analyses, numerous SBC’s taxa (i.e., leading biomarkers) were principally altered when treated with different planted types and N forms (Figure S6).

4. Discussion

The results of this study demonstrated that BP resulted in a notable increase in soil pH in comparison to the control. As a result, the soil undergoes alkalization rather than acidification as a consequence of the B. pilosa invasion. This finding is likely attributable to the exudation of alkaline substances or other substances that can trigger the alkaline effect, such as anions, during the growth of B. pilosa [59,60,61,62]. Furthermore, this phenomenon may be attributed to a decrease in the exudation of hydrogen ions via a decrease in the release of acid-containing substances present in the root exudates of B. pilosa [8,63,64,65]. Additionally, the alkalization of soil under B. pilosa invasion may be attributed to the selective absorption of different forms of N components in soil by B. pilosa, a phenomenon that has been observed in numerous other IPs [66,67,68,69]. In particular, BP was observed to significantly decrease soil ammonium content in comparison to the control. Consequently, B. pilosa exhibits a preference for ammonium absorption over other nitrogenous components, a trait that has also been observed in other plants (including other IPS) [40,70,71]. This finding may indicate that the uptake capacity and utilization efficiency of ammonium by B. pilosa may be greater than those of other forms of N components, primarily due to the lower energy cost associated with ammonium uptake and utilization [72,73].
BP exhibited a notable reduction in soil moisture in comparison to the control. This finding may be attributed to the rapid evapotranspiration rate of IPS, which is mediated by their rapid growth pattern, especially high water-use efficiency [74,75,76,77].
A notable reduction in soil electrical conductivity was observed under BP in comparison to the control. This finding may be attributed to a reduction in the exudation of secondary compounds, especially root exudates, of B. pilosa, which has resulted in a decrease in soil water-soluble salt content. Prior research has indicated a strong correlation between the exudate profiles of plants and soil electrical conductivity [78,79,80,81].
BPPL resulted in a notable enhancement in total soil organic C content compared to the control. This phenomenon may be attributed to the increased content of soil C, which is the result of the contributions of C-containing substances from the two plants to the soil, leading to C sequestration in the soil [61,82,83,84]. Thus, soil organic C content can be increased under BPPL. It can, therefore, be concluded that there is a greater potential for organic C to be sequestered in soil, particularly through the utilization of C by soil microorganisms. The results of this study indicate that BPPL may serve as a vital C sink in soil rather than a C emitter through the process of C sequestration in soil. It can thus be argued that BPPL may contribute to the alleviation of climate change rather than its exacerbation. It can thus be proposed that, although IPs have a negative ecological impact in many cases, they can also be transformed into a valuable resource if managed properly, at least in terms of their impact on soil organic C content.
It has been demonstrated that the introduction of IPs can result in alterations to soil enzymatic activities [40,85,86] and SBC’s alpha diversity [87,88,89,90]. This is attributed to the release of nutrients (especially C/N-containing substances) through the decomposition of litter and/or the exudation of root substances during the growth process of the plants. Inconsistent with the first hypothesis, BP markedly reduced the activities of polyphenol oxidase, β-xylosidase, FDA hydrolase, and sucrase in the soil in comparison to the control. It can thus be concluded that the ability of polyphenols to oxidize, the ability of xylan degradation, the ability of FDA to hydrolyze, and the ability of sucrose to hydrolyze in soil decreased as a consequence of B. pilosa invasion. The observed decline in soil enzymatic activities may be attributed to a reduction in the nutrient availability level in the soil and/or an increase in SBC’s metabolic rate under B. pilosa invasion. Inconsistent with the first hypothesis, BP also exhibited a marked reduction in all SBC’s alpha diversity indices (with the exception of Simpson’s dominance index) in comparison to PL. Furthermore, previous studies have demonstrated that IPs can reduce SBC’s alpha diversity [87,88,89,90]. The reduction in SBC’s alpha diversity observed in the presence of B. pilosa invasion may be attributed to a number of issues, e.g., the elevated soil pH and the reduced moisture, electrical conductivity, ammonium content, and enzymatic activities. In particular, these indicators may have a significant impact on SBC’s diversity and abundance, primarily through the fluctuations in resource use and access to nutrients metabolized by SBC. Furthermore, the aforementioned indicators also demonstrated a robust correlation with SBC’s alpha diversity, as evidenced by the findings of the correlation analysis and PCA. Moreover, BP resulted in notable alterations to SBC’s beta diversity, with the appearance of several leading SBC’s biomarkers. This phenomenon may be attributed to the differences in the root exudates of the two plants, which have caused a certain degree of differentiation at the species level in SBC. In particular, the presence of several principal SBC’s biomarkers may be attributed to alterations in the form, amount, and complexity of nutrients (e.g., C/N-containing substances) in soil. These alterations result in selective facilitative or inhibitory effects on SBC. Consequently, some of SBC’s taxa are able to flourish, while others may become eradicated over time due to the encroachment of B. pilosa. As a result, the invasion of B. pilosa exerts a notable influence not only on SBC’s alpha diversity but also on SBC’s community composition.
The study demonstrated that soil FDA hydrolase activity and SBC’s alpha diversity, especially the indices of Shannon’s diversity, Simpson’s dominance, and Pielou’s evenness, exhibited a pronounced decline in response to nitrate treatment in BPPL treated with nitrate compared to those under BPPL when compared to those treated with ammonium, urea, and mixed N. This result is consistent with the second hypothesis. This finding can be attributed to the stronger reduction in soil moisture and electrical conductivity treated with nitrate compared to that treated with ammonium, urea, and mixed N. In particular, soil moisture [81,91,92,93] and electrical conductivity [81,94,95,96] are generally considered to be the main drivers of SBC’s diversity and abundance, mainly via the fluctuations in resource use and access to nutrients metabolized by SBC. Furthermore, the findings of the correlation analysis and PCA indicated a robust correlation between soil moisture, electrical conductivity, and SBC’s alpha diversity. In addition, all forms of N appeared to regulate several principal SBC’s biomarkers in either an up- or down-regulatory manner. This result may be attributed to the differing N-phototrophic capabilities of the principal SBC’s biomarkers. It can be postulated that the diverse forms of nitrogen may exert disparate selection pressures on the heterogeneous taxa of the principal SBC’s biomarkers, resulting in an expansion of N-phototrophic SBC taxa and a contraction of N-sensitive SBC taxa. It can be concluded that the N form primarily affects the composition of the soil bacterial community rather than its alpha diversity.

5. Conclusions

This study represents the inaugural attempt to clarify the effects of B. pilosa on soil physicochemical properties, soil C and N contents, soil enzymatic activities, and SBC’s community composition in comparison to P. laciniata treated with simulated N deposition at 5 g N m−2 yr−1 in four forms (nitrate, ammonium, urea, and mixed N). The primary findings are as follows: (1) BP caused a noteworthy elevation in soil pH, accompanied by a pronounced reduction in the moisture, electrical conductivity, ammonium content, and the activities of polyphenol oxidase, β-xylosidase, FDA hydrolase, and sucrase in soil when compared to the control. (2) BPPL mediated a substantial reduction in total soil organic C content compared to the control. (3) BP recruited a marked decrease in all SBC’s alpha diversity indices (with the exception of the Simpson’s dominance index) compared to PL. (4) Soil FDA hydrolase activity and SBC’s alpha diversity, in particular the indices of Shannon’s diversity, Simpson’s dominance, and Pielou’s evenness, were found to be significantly lower in BPPL treated with nitrate than in BPPL treated with ammonium, urea, and mixed N.

Supplementary Materials

The following supporting information can be downloaded at: https://www.mdpi.com/article/10.3390/microorganisms12081624/s1, Table S1: Two-way ANOVA on the influences of planted type and nitrogen form on soil physicochemical properties, soil carbon and nitrogen contents, soil enzymatic activities, and soil bacterial alpha diversity; Table S2: Correlations (r) between soil physicochemical properties, soil carbon and nitrogen contents, soil enzymatic activities, and soil bacterial alpha diversity; Figure S1: The geographical location (Zhenjiang, Jiangsu, China) of the sampled zone (square with red) in this study; Figure S2: PCoA of beta diversity estimates of soil bacterial communities based on the weighted UniFrac distance; Figure S3: NMDS of beta diversity estimates of soil bacterial communities based on the weighted UniFrac distance; Figure S4: Heatmap of beta diversity estimates of soil bacterial communities based on the weighted UniFrac distance at the family level. The color blocks represent the distance values; Figure S5: Bubble chart of soil bacterial biomarkers at the class level; Figure S6: LEfSe method identifies the significantly different abundant taxa of soil bacterial communities with different treatments.

Author Contributions

Y.L. (Yingsheng Liu): data curation, investigation, methodology, and writing—review and editing; Y.D.: data curation, investigation, methodology, and writing—review and editing; Y.L. (Yue Li): data curation, investigation, methodology, and writing—review and editing; C.L.: data curation, investigation, methodology, and writing—review and editing; S.Z.: data curation, investigation, methodology, and writing—review and editing; Z.X.: data curation, investigation, methodology, and writing—review and editing; C.W.: conceptualization, formal analysis, funding acquisition, project administration, supervision, and writing—original draft preparation; D.D.: funding acquisition, project administration, writing—review and editing. All authors have read and agreed to the published version of the manuscript.

Funding

This study was funded by a research project on the application of invasive plants in soil ecological restoration in Jiangsu (20240110), the National Natural Science Foundation of China (32071521), the Special Research Project of the School of Emergency Management, Jiangsu University (KY-C-01), the Carbon Peak and Carbon Neutrality Technology Innovation Foundation of Jiangsu Province (BK20220030), and the Jiangsu Collaborative Innovation Center of Technology and Material of Water Treatment.

Informed Consent Statement

Informed consent was obtained from all subjects involved in the study.

Data Availability Statement

The raw data supporting the conclusions of this article will be made available by the authors on request.

Acknowledgments

We greatly appreciate the anonymous reviewers for the insightful comments that greatly improved this manuscript.

Conflicts of Interest

The authors declare no conflicts of interest.

References

  1. Li, C.; Li, Y.; Xu, Z.L.; Zhong, S.S.; Cheng, H.Y.; Liu, J.; Yu, Y.L.; Wang, C.Y.; Du, D.L. The effects of co-invasion by three Asteraceae invasive alien species on plant taxonomic and functional diversity in herbaceous ruderal communities in southern Jiangsu, China. Biol. Futura 2024, 75, 205–217. [Google Scholar] [CrossRef] [PubMed]
  2. Forey, E.; Lodhar, S.Y.F.; Galvin, S.D.; Lowry, J.H.; Gopaul, S.; Hanson, G.; Carboni, M.; Chauvat, M.; Boehmer, H.J. Alien palm invasion leads to selective biotic filtering of resident plant communities towards competitive functional traits. Biol. Invasions 2023, 25, 1489–1508. [Google Scholar] [CrossRef]
  3. Mohanty, N.P.; Crottini, A.; Garcia, R.A.; Measey, J. Non-native populations and global invasion potential of the Indian bullfrog Hoplobatrachus tigerinus: A synthesis for risk-analysis. Biol. Invasions 2021, 23, 69–81. [Google Scholar] [CrossRef]
  4. Sharma, A.; Kaur, A.; Kohli, R.K.; Singh, H.P.; Batish, D.R. Bidens pilosa (Asteraceae) invasion reshapes the pattern of plant communities and edaphic properties across the north-western Himalayan landscape. Ecol. Inform. 2023, 77, 102281. [Google Scholar] [CrossRef]
  5. Yan, X.L.; Liu, Q.R.; Shou, H.Y.; Zeng, X.F.; Zhang, Y.; Chen, L.; Liu, Y.; Ma, H.Y.; Qi, S.Y.; Ma, J.S. The categorization and analysis on the geographic distribution patterns of Chinese alien invasive plants. Biodivers. Sci. 2014, 22, 667–676. [Google Scholar]
  6. Kone, A.W.; Kassi, S.P.A.Y.; Koffi, B.Y.; Masse, D.; Maiga, A.A.; Tondoh, J.E.; Kisaka, O.M.; Toure, G.P.T. Chromolaena odorata (L.) K&R (Asteraceae) invasion effects on soil microbial biomass and activities in a forest-savanna mosaic. Catena 2021, 207, 105619. [Google Scholar]
  7. Sotes, G.J.; Cavieres, L.A.; Gomez-Gonzalez, S. High competitive ability of Centaurea melitensis L. (Asteraceae) does not increase in the invaded range. Biol. Invasions 2021, 23, 693–703. [Google Scholar] [CrossRef]
  8. Raghurama, M.; Sankaran, M. Invasive nitrogen-fixing plants increase nitrogen availability and cycling rates in a montane tropical grassland. Plant Ecol. 2022, 223, 13–26. [Google Scholar] [CrossRef]
  9. Ren, B.H.; Meng, M.; Yu, J.X.; Ma, X.W.; Li, D.Y.; Li, J.H.; Yang, J.Y.; Bai, L.; Feng, Y.L. Invasion by Cenchrus spinifex changes the soil microbial community structure in a sandy grassland ecosystem. Heliyon 2023, 9, e20860. [Google Scholar] [CrossRef]
  10. Stanek, M.; Zubek, S.; Stefanowicz, A.M. Differences in phenolics produced by invasive Quercus rubra and native plant communities induced changes in soil microbial properties and enzymatic activity. For. Ecol. Manag. 2021, 482, 118901. [Google Scholar] [CrossRef]
  11. Jurksiene, G.; Janusauskaite, D.; Baliuckas, V. Microbial community analysis of native Pinus sylvestris L. and alien Pinus mugo L. on dune sands as determined by ecoplates. Forests 2020, 11, 1202. [Google Scholar] [CrossRef]
  12. Kuypers, M.M.M.; Marchant, H.K.; Kartal, B. The microbial nitrogen-cycling network. Nat. Rev. Microbiol. 2018, 16, 263–276. [Google Scholar] [CrossRef] [PubMed]
  13. Yu, H.X.; Le Roux, J.J.; Jiang, Z.Y.; Sun, F.; Peng, C.L.; Li, W.H. Soil nitrogen dynamics and competition during plant invasion: Insights from Mikania micrantha invasions in China. New Phytol. 2021, 229, 3440–3452. [Google Scholar] [CrossRef] [PubMed]
  14. Francis, C.A.; Beman, J.M.; Kuypers, M.M.M. New processes and players in the nitrogen cycle: The microbial ecology of anaerobic and archaeal ammonia oxidation. ISME J. 2007, 1, 19–27. [Google Scholar] [CrossRef] [PubMed]
  15. van den Elzen, E.; van den Berg, L.J.L.; van der Weijden, B.; Fritz, C.; Sheppard, L.J.; Lamers, L.P.M. Effects of airborne ammonium and nitrate pollution strongly differ in peat bogs, but symbiotic nitrogen fixation remains unaffected. Sci. Total Environ. 2018, 610–611, 732–740. [Google Scholar] [CrossRef] [PubMed]
  16. Li, Q.W.; Zhang, X.Y.; Liang, J.F.; Gao, J.Q.; Xu, X.L.; Yu, F.H. High nitrogen uptake and utilization contribute to the dominance of invasive Spartina alterniflora over native Phragmites australis. Biol. Fertil. Soils 2021, 57, 1007–1013. [Google Scholar] [CrossRef]
  17. Parepa, M.; Fischer, M.; Bossdorf, O. Environmental variability promotes plant invasion. Nat. Commun. 2013, 4, 1604. [Google Scholar] [CrossRef] [PubMed]
  18. Feng, Y.L.; Lei, Y.B.; Wang, R.F.; Callaway, R.M.; Alfonso, V.B.; Inderjit; Li, Y.P.; Zheng, Y.L. Evolutionary tradeoffs for nitrogen allocation to photosynthesis versus cell walls in an invasive plant. Proc. Natl. Acad. Sci. USA 2009, 106, 1853–1856. [Google Scholar] [CrossRef] [PubMed]
  19. Mantoani, M.C.; Gonzalez, A.B.; Sancho, L.G.; Osborne, B.A. Growth, phenology and N-utilization by invasive populations of Gunnera tinctoria. J. Plant Ecol. 2020, 13, 589–600. [Google Scholar] [CrossRef]
  20. Davidson, A.M.; Jennions, M.; Nicotra, A.B. Do invasive species show higher phenotypic plasticity than native species and, if so, is it adaptive? A meta-analysis. Ecol. Lett. 2011, 14, 419–431. [Google Scholar] [CrossRef]
  21. Kamutando, C.N.; Vikram, S.; Kamgan-Nkuekam, G.; Makhalanyane, T.P.; Greve, M.; Le Roux, J.J.; Richardson, D.M.; Cowan, D.; Valverde, A. Soil nutritional status and biogeography influence rhizosphere microbial communities associated with the invasive tree Acacia dealbata. Sci. Rep. 2017, 7, 6472. [Google Scholar] [CrossRef] [PubMed]
  22. Xu, C.W.; Yang, M.Z.; Chen, Y.J.; Chen, L.M.; Zhang, D.Z.; Mei, L.; Shi, Y.T.; Zhang, H.B. Changes in non-symbiotic nitrogen-fixing bacteria inhabiting rhizosphere soils of an invasive plant Ageratina adenophora. Appl. Soil Ecol. 2012, 54, 32–38. [Google Scholar] [CrossRef]
  23. Li, J.; He, J.Z.; Liu, M.; Yan, Z.Q.; Xu, X.L.; Kuzyakov, Y. Invasive plant competitivity is mediated by nitrogen use strategies and rhizosphere microbiome. Soil Biol. Biochem. 2024, 192, 109361. [Google Scholar] [CrossRef]
  24. Davis, M.A.; Pelsor, M. Experimental support for a resource-based mechanistic model of invasibility. Ecol. Lett. 2001, 4, 421–428. [Google Scholar] [CrossRef]
  25. Guo, Q.F.; Fei, S.J.; Dukes, J.S.; Oswalt, C.M.; Iannone III, B.V.; Potter, K.M. A unified approach for quantifying invasibility and degree of invasion. Ecology 2015, 96, 2613–2621. [Google Scholar] [CrossRef] [PubMed]
  26. Rijal, D.P.; Alm, T.; Nilsen, L.; Alsos, I.G. Giant invasive Heracleum persicum: Friend or foe of plant diversity? Ecol. Evol. 2017, 7, 4936–4950. [Google Scholar] [CrossRef] [PubMed]
  27. Chen, H.Y.; Huang, S.Z. Composition and supply of inorganic and organic nitrogen species in dry and wet atmospheric deposition: Use of organic nitrogen composition to calculate the Ocean’s external nitrogen flux from the atmosphere. Cont. Shelf Res. 2021, 213, 104316. [Google Scholar] [CrossRef]
  28. Yang, Y.; Liu, L.; Zhang, F.; Zhang, X.; Xu, W.; Liu, X.; Li, Y.; Wang, Z.; Xie, Y. Enhanced nitrous oxide emissions caused by atmospheric nitrogen deposition in agroecosystems over China. Environ. Sci. Pollut. Res. 2021, 28, 15350–15360. [Google Scholar] [CrossRef]
  29. Yang, Y.Y.; Liu, L.; Zhang, F.; Zhang, X.Y.; Xu, W.; Liu, X.J.; Wang, Z.; Xie, Y.W. Soil nitrous oxide emissions by atmospheric nitrogen deposition over global agricultural systems. Environ. Sci. Technol. 2021, 55, 4420–4429. [Google Scholar] [CrossRef]
  30. Dentener, F.; Drevet, J.; Lamarque, J.F.; Bey, I.; Eickhout, B.; Fiore, A.M.; Hauglustaine, D.; Horowitz, L.W.; Krol, M.; Kulshrestha, U.C.; et al. Nitrogen and sulfur deposition on regional and global scales: A multimodel evaluation. Glob. Biogeochem. Cycles 2006, 20, GB4003. [Google Scholar] [CrossRef]
  31. Fu, Y.D.; Xu, W.; Wen, Z.; Han, M.J.; Sun, J.H.; Tang, A.H.; Liu, X. Enhanced atmospheric nitrogen deposition at a rural site in northwest China from 2011 to 2018. Atmos. Res. 2020, 245, 105071. [Google Scholar] [CrossRef]
  32. Zhu, J.X.; Chen, Z.; Wang, Q.F.; Xu, L.; He, N.P.; Jia, Y.L.; Zhang, Q.Y.; Yu, G.R. Potential transition in the effects of atmospheric nitrogen deposition in China. Environ. Pollut. 2020, 258, 113739. [Google Scholar] [CrossRef] [PubMed]
  33. Xu, W.; Zhang, L.; Liu, X.J. A database of atmospheric nitrogen concentration and deposition from the nationwide monitoring network in China. Sci. Data 2019, 6, 51. [Google Scholar] [CrossRef] [PubMed]
  34. Chang, C.T.; Yang, C.J.; Huang, K.H.; Huang, J.C.; Lin, T.C. Changes of precipitation acidity related to sulfur and nitrogen deposition in forests across three continents in north hemisphere over last two decades. Sci. Total Environ. 2022, 806, 150552. [Google Scholar] [CrossRef] [PubMed]
  35. McDonnell, T.C.; Driscoll, C.T.; Sullivan, T.J.; Burns, D.A.; Baldigo, B.P.; Shao, S.; Lawrence, G.B. Regional target loads of atmospheric nitrogen and sulfur deposition for the protection of stream and watershed soil resources of the Adirondack Mountains, USA. Environ. Pollut. 2021, 281, 117110. [Google Scholar] [CrossRef] [PubMed]
  36. Huang, J.; Zhu, W.X.; Ren, H.; Chen, H.F.; Wang, J. Impact of atmospheric nitrogen deposition on soil properties and herb-layer diversity in remnant forests along an urban-rural gradient in Guangzhou, southern China. Plant Ecol. 2012, 213, 1187–1202. [Google Scholar] [CrossRef]
  37. Guo, P.; Kong, D.Y.; Yang, L.F.; Sun, X. Differences in characteristics of sample sites explain variable responses of soil microbial biomass to nitrogen addition: A meta-analysis. Ecosystems 2023, 26, 1703–1715. [Google Scholar] [CrossRef]
  38. Ren, G.Q.; Yang, B.; Cui, M.M.; Dai, Z.C.; Xiang, Y.; Zhang, H.Y.; Li, G.L.; Li, J.; Javed, Q.; Du, D.L. Warming and elevated nitrogen deposition accelerate the invasion process of Solidago canadensis L. Ecol. Process. 2022, 11, 62. [Google Scholar] [CrossRef]
  39. Ding, W.L.; Xu, W.Z.; Gao, Z.J.; Xu, B.C. Effects of water and nitrogen on growth and relative competitive ability of introduced versus native C-4 grass species in the semi-arid Loess Plateau of China. J. Arid. Land 2021, 13, 730–743. [Google Scholar] [CrossRef]
  40. Zhong, S.S.; Xu, Z.L.; Yu, Y.L.; Liu, J.; Wang, Y.Y.; Guo, E.; Wang, C.Y. Rhus typhina decreased soil nitrogen contents and peroxidase activity following the addition of nitrogen. Int. J. Environ. Sci. Technol. 2023, 111, 17–22. [Google Scholar] [CrossRef]
  41. Sparrius, L.B.; Kooijman, A.M. Invasiveness of Campylopus introflexus in drift sands depends on nitrogen deposition and soil organic matter. Appl. Veg. Sci. 2011, 14, 221–229. [Google Scholar] [CrossRef]
  42. Cornell, S.E. Atmospheric nitrogen deposition: Revisiting the question of the importance of the organic component. Environ. Pollut. 2011, 159, 2214–2222. [Google Scholar] [CrossRef] [PubMed]
  43. Cornell, S.E.; Jickells, T.D.; Cape, J.N.; Rowland, A.P.; Duce, R.A. Organic nitrogen deposition on land and coastal environments: A review of methods and data. Atmos. Environ. 2003, 37, 2173–2191. [Google Scholar] [CrossRef]
  44. Jiang, C.M.; Yu, W.T.; Ma, Q.; Xu, Y.G.; Zou, H.; Zhang, S.C.; Sheng, W.P. Atmospheric organic nitrogen deposition: Analysis of nationwide data and a case study in Northeast China. Environ. Pollut. 2013, 182, 430–436. [Google Scholar] [CrossRef] [PubMed]
  45. Kanakidou, M.; Myriokefalitakis, S.; Daskalakis, N.; Fanourgakis, G.; Nenes, A.; Baker, A.R.; Tsigaridis, K.; Mihalopoulos, N. Past, present, and future atmospheric nitrogen deposition. J. Atmos. Sci. 2016, 73, 2039–2047. [Google Scholar] [CrossRef] [PubMed]
  46. Mircea, D.M.; Calone, R.; Estrelles, E.; Soriano, P.; Sestras, R.E.; Boscaiu, M.; Sestras, A.F.; Vicente, O. Responses of different invasive and non-invasive ornamental plants to water stress during seed germination and vegetative growth. Sci. Rep. 2023, 13, 13281. [Google Scholar] [CrossRef] [PubMed]
  47. Gao, F.L.; He, Q.S.; Xie, R.Q.; Hou, J.H.; Shi, C.L.; Li, J.M.; Yu, F.H. Interactive effects of nutrient availability, fluctuating supply, and plant parasitism on the post-invasion success of Bidens pilosa. Biol. Invasions 2021, 23, 3035–3046. [Google Scholar] [CrossRef]
  48. Li, C.; Li, Y.; Zhong, S.S.; Xu, Z.L.; Xu, Z.Y.; Zhu, M.W.; Wei, Y.Q.; Wang, C.Y.; Du, D.L. Do the leaves of multiple invasive plants decompose more easily than a native plant’s under nitrogen deposition with different forms? Nitrogen 2024, 5, 202–218. [Google Scholar] [CrossRef]
  49. Luo, X.S.; Liu, X.J.; Pan, Y.P.; Wen, Z.; Xu, W.; Zhang, L.; Kou, C.L.; Lv, J.L.; Goulding, K. Atmospheric reactive nitrogen concentration and deposition trends from 2011 to 2018 at an urban site in north China. Atmos. Environ. 2020, 224, 117298. [Google Scholar] [CrossRef]
  50. Zhang, Y.; Song, L.; Liu, X.J.; Li, W.Q.; Lu, S.H.; Zheng, L.X.; Bai, Z.C.; Cai, G.Y.; Zhang, F.S. Atmospheric organic nitrogen deposition in China. Atmos. Environ. 2012, 46, 195–204, Erratum in Atmos. Environ. 2012, 49, 422. [Google Scholar] [CrossRef]
  51. Galloway, J.N.; Townsend, A.R.; Erisman, J.W.; Bekunda, M.; Cai, Z.; Freney, J.R.; Martinelli, L.A.; Seitzinger, S.P.; Sutton, M.A. Transformation of the nitrogen cycle: Recent trends, questions, and potential solutions. Science 2008, 320, 889–892. [Google Scholar] [CrossRef] [PubMed]
  52. Brookes, P.C.; Landman, A.; Pruden, G.; Jenkinson, D.S. Chloroform fumigation and the release of soil nitrogen: A rapid direct extraction method to measure microbial biomass nitrogen in soil. Soil Biol. Biochem. 1985, 17, 837–842. [Google Scholar] [CrossRef]
  53. Vance, E.D.; Brookes, P.C.; Jenkinson, D.S. An extraction method for measuring soil microbial biomass C. Soil Biol. Biochem. 1987, 19, 703–707. [Google Scholar] [CrossRef]
  54. Ma, W.J.; Li, J.; Gao, Y.; Xing, F.; Sun, S.N.; Zhang, T.; Zhu, X.Z.; Chen, C.; Li, Z. Responses of soil extracellular enzyme activities and microbial community properties to interaction between nitrogen addition and increased precipitation in a semi-arid grassland ecosystem. Sci. Total Environ. 2020, 703, 134691. [Google Scholar] [CrossRef] [PubMed]
  55. Cui, J.; Wang, J.J.; Xu, J.; Xu, C.H.; Xu, X.N. Changes in soil bacterial communities in an evergreen broad-leaved forest in east China following 4 years of nitrogen addition. J. Soils Sediments 2017, 17, 2156–2164. [Google Scholar] [CrossRef]
  56. GB/T 42485-2023; Soil Quality-Determination of Nitrate, Nitrite and Ammonium in Soils-Extraction with Potassium Chloride Solution and Determination with Manual Method. National Standard of China. State Administration for Market Regulation of China and Standardization Administration of China: Beijing, China, 2023.
  57. Klindworth, A.; Pruesse, E.; Schweer, T.; Peplies, J.; Quast, C.; Horn, M.; Glöckner, F.O. Evaluation of general 16S ribosomal RNA gene PCR primers for classical and next-generation sequencing-based diversity studies. Nucleic Acids Res. 2013, 41, e1. [Google Scholar] [CrossRef] [PubMed]
  58. Wear, E.K.; Wilbanks, E.G.; Nelson, C.E.; Carlson, C.A. Primer selection impacts specific population abundances but not community dynamics in a monthly time-series 16S rRNA gene amplicon analysis of coastal marine bacterioplankton. Environ. Microbiol. 2018, 20, 2709–2726. [Google Scholar] [CrossRef] [PubMed]
  59. Guo, X.; Xu, Z.W.; Li, M.Y.; Ren, X.H.; Liu, J.; Guo, W.H. Increased soil moisture aggravated the competitive effects of the invasive tree Rhus typhina on the native tree Cotinus coggygria. BMC Ecol. 2020, 20, 17. [Google Scholar] [CrossRef] [PubMed]
  60. Fröhlich, B.; Niemetz, R.; Gross, G.G. Gallotannin biosynthesis: Two new galloyltransferases from Rhus typhina leaves preferentially acylating hexa- and heptagalloylglucoses. Planta 2002, 216, 168–172. [Google Scholar] [CrossRef]
  61. Stefanowicz, A.M.; Zubek, S.; Stanek, M.; Grzes, L.M.; Rozej-Pabijan, E.; Blaszkowski, J.; Woch, M.W. Invasion of Rosa rugosa induced changes in soil nutrients and microbial communities of coastal sand dunes. Sci. Total Environ. 2019, 677, 340–349. [Google Scholar] [CrossRef]
  62. Sharma, G.P.; Raghubanshi, A.S. Lantana invasion alters soil nitrogen pools and processes in the tropical dry deciduous forest of India. Appl. Soil Ecol. 2009, 42, 134–140. [Google Scholar] [CrossRef]
  63. Chen, Z.H.; Li, Y.C.; Chang, S.X.; Xu, Q.F.; Li, Y.F.; Ma, Z.L.; Qin, H.; Cai, Y.J. Linking enhanced soil nitrogen mineralization to increased fungal decomposition capacity with Moso bamboo invasion of broadleaf forests. Sci. Total Environ. 2021, 771, 144779. [Google Scholar] [CrossRef]
  64. Wang, C.Y.; Jiang, K.; Zhou, J.W.; Liu, J.; Wu, B.D. Responses of soil N-fixing bacterial communities to redroot pigweed (Amaranthus retroflexus L.) invasion under Cu and Cd heavy metal soil pollution. Agric. Ecosyst. Environ. 2018, 267, 15–22. [Google Scholar] [CrossRef]
  65. Zhong, S.S.; Xu, Z.L.; Yu, Y.L.; Cheng, H.Y.; Wang, S.; Wei, M.; Du, D.L.; Wang, C.Y. Acid deposition at higher acidity weakens the antagonistic responses during the co-decomposition of two Asteraceae invasive plants. Ecotoxicol. Environ. Saf. 2022, 243, 114012. [Google Scholar] [CrossRef]
  66. Ehrenfeld, J.G. Effects of exotic plant invasions on soil nutrient cycling processes. Ecosystems 2003, 6, 503–523. [Google Scholar] [CrossRef]
  67. Kuebbing, S.E.; Classen, A.T.; Simberloff, D. Two co-occurring invasive woody shrubs alter soil properties and promote subdominant invasive species. J. Appl. Ecol. 2014, 51, 124–133. [Google Scholar] [CrossRef]
  68. Fan, L.; Chen, Y.; Yuan, J.G.; Yang, Z.Y. The effect of Lantana camara Linn. invasion on soil chemical and microbiological properties and plant biomass accumulation in southern China. Geoderma 2010, 154, 370–378. [Google Scholar] [CrossRef]
  69. Souza-Alonso, P.; Guisande-Collazo, A.; González, L. Gradualism in Acacia dealbata Link invasion: Impact on soil chemistry and microbial community over a chronological sequence. Soil Biol. Biochem. 2015, 80, 315–323. [Google Scholar] [CrossRef]
  70. Huang, Q.Q.; Xu, H.; Fan, Z.W.; Hou, Y.P. Effects of Rhus typhina invasion into young Pinus thunbergii forests on soil chemical properties. Ecol. Environ. Sci. 2013, 22, 1119–1123. [Google Scholar]
  71. Hou, Y.P.; Liu, L.; Chu, H.; Ma, S.J.; Zhao, D.; Liang, R.R. Effects of exotic plant Rhus typhina invasion on soil properties in different forest types. Acta Ecol. Sin. 2015, 35, 5324–5330. [Google Scholar]
  72. Kronzucker, H.J.; Britto, D.T.; Davenport, R.J.; Tester, M. Ammonium toxicity and the real cost of transport. Trends Plant Sci. 2001, 6, 335–337. [Google Scholar] [CrossRef] [PubMed]
  73. Guo, S.W.; Zhou, Y.; Shen, Q.R.; Zhang, F.S. Effect of ammonium and nitrate nutrition on some physiological processes in higher plants—Growth, photosynthesis, photorespiration, and water relations. Plant Biol. 2007, 9, 21–29. [Google Scholar] [CrossRef]
  74. Wang, C.Y.; Jiang, K.; Zhou, J.W.; Xiao, H.G.; Wang, L. Responses of soil bacterial communities to Conyza canadensis invasion with different cover classes along a climatic gradient. Clean 2018, 46, 1800212. [Google Scholar] [CrossRef]
  75. van Kleunen, M.; Weber, E.; Fischer, M. A meta-analysis of trait differences between invasive and non-invasive plant species. Ecol. Lett. 2010, 13, 235–245. [Google Scholar] [CrossRef] [PubMed]
  76. Godoy, O.; Valladares, F.; Pilar, C.-D. Multispecies comparison reveals that invasive and native plants differ in their traits but not in their plasticity. Funct. Ecol. 2011, 25, 1248–1259. [Google Scholar] [CrossRef]
  77. Dassonville, N.; Guillaumaud, N.; Piola, F.; Meerts, P.; Poly, F. Niche construction by the invasive Asian knotweeds (species complex Fallopia): Impact on activity, abundance and community structure of denitrifiers and nitrifiers. Biol. Invasions 2011, 13, 1115–1133. [Google Scholar] [CrossRef]
  78. Liu, S.L.; Maimaitiaili, B.; Joergensen, R.G.; Feng, G. Response of soil microorganisms after converting a saline desert to arable land in central Asia. Appl. Soil Ecol. 2016, 98, 1–7. [Google Scholar] [CrossRef]
  79. Chang, C.L.; Fu, X.P.; Zhou, X.G.; Guo, M.Y.; Wu, F.Z. Effects of seven different companion plants on cucumber productivity, soil chemical characteristics and Pseudomonas community. J. Integr. Agric. 2017, 16, 2206–2214. [Google Scholar] [CrossRef]
  80. Wu, X.; Wu, H.; Ye, J.Y.; Zhong, B. Study on the release routes of allelochemicals from Pistia stratiotes Linn., and its anti-cyanobacteria mechanisms on Microcystis aeruginosa. Environ. Sci. Pollut. Res. 2015, 22, 18994–19001. [Google Scholar] [CrossRef]
  81. Wang, C.Y.; Wei, M.; Wang, S.; Wu, B.D.; Du, D.L. Cadmium influences the litter decomposition of Solidago canadensis L. and soil N-fixing bacterial communities. Chemosphere 2020, 246, 125717. [Google Scholar] [CrossRef]
  82. Ahmad, R.; Khuroo, A.A.; Hamid, M.; Rashid, I. Plant invasion alters the physico-chemical dynamics of soil system: Insights from invasive Leucanthemum vulgare in the Indian Himalaya. Environ. Monit. Assess. 2020, 191, 792. [Google Scholar] [CrossRef]
  83. Vujanović, D.; Losapio, G.; Milić, S.; Milić, D. The impact of multiple species invasion on soil and plant communities increases with invasive species co-occurrence. Front. Plant Sci. 2022, 13, 875824. [Google Scholar] [CrossRef] [PubMed]
  84. Zhang, G.; Bai, J.; Wang, W.; Jia, J.; Huang, L.; Kong, F.; Xi, M. Plant invasion reshapes the latitudinal pattern of soil microbial necromass and its contribution to soil organic carbon in coastal wetlands. Catena 2023, 222, 106859. [Google Scholar] [CrossRef]
  85. Ge, Y.Y.; Wang, Q.L.; Wang, L.; Liu, W.X.; Liu, X.Y.; Huang, Y.J.; Christie, P. Response of soil enzymes and microbial communities to root extracts of the alien Alternanthera philoxeroides. Arch. Agron. Soil Sci. 2018, 64, 708–717. [Google Scholar] [CrossRef]
  86. Yu, Y.L.; Xu, Z.L.; Zhong, S.S.; Cheng, H.Y.; Guo, E.R.; Wang, C.Y. The co-invasion of the three Asteraceae invasive plants can synergistically increase soil phenol oxidase activity. Biol. Bull. 2023, 50, 467–473. [Google Scholar]
  87. Lazzaro, L.; Giuliani, C.; Fabiani, A.; Agnelli, A.E.; Pastorelli, R.; Lagomarsino, A.; Benesperi, R.; Calamassi, R.; Foggi, B. Soil and plant changing after invasion: The case of Acacia dealbata in a Mediterranean ecosystem. Sci. Total Environ. 2014, 497–498, 491–498. [Google Scholar] [CrossRef] [PubMed]
  88. Slabbert, E.; Jacobs, S.M.; Jacobs, K. The soil bacterial communities of South African fynbos riparian ecosystems invaded by Australian Acacia species. PLoS ONE 2014, 9, e86560. [Google Scholar] [CrossRef] [PubMed]
  89. Yang, W.; Jeelani, N.; Zhu, Z.; Luo, Y.; Cheng, X.; An, S. Alterations in soil bacterial community in relation to Spartina alterniflora Loisel. invasion chronosequence in the eastern Chinese coastal wetlands. Appl. Soil Ecol. 2019, 135, 38–43. [Google Scholar] [CrossRef]
  90. Zhu, P.; Wei, W.; Bai, X.F.; Wu, N.; Hou, Y.P. Effects of invasive Rhus typhina L. on bacterial diversity and community composition in soil. Ecoscience 2020, 27, 177–184. [Google Scholar] [CrossRef]
  91. Han, Y.J.; Wang, G.S.; Xiong, L.H.; Xu, Y.; Li, S. Rainfall effect on soil respiration depends on antecedent soil moisture. Sci. Total Environ. 2024, 926, 172130. [Google Scholar] [CrossRef]
  92. Ansari, J.; Bardhan, S.; Eivazi, F.; Anderson, S.H.; Mendis, S.S. Bacterial community diversity for three selected land use systems as affected by soil moisture regime. Appl. Soil Ecol. 2023, 192, 105100. [Google Scholar] [CrossRef]
  93. Shawver, S.; Ishii, S.; Strickland, M.S.; Badgley, B. Soil type and moisture content alter soil microbial responses to manure from cattle administered antibiotics. Environ. Sci. Pollut. Res. 2024, 31, 27259–27272. [Google Scholar] [CrossRef] [PubMed]
  94. Johnson, M.J.; Lee, K.Y.; Scow, K.M. DNA fingerprinting reveals links among agricultural crops, soil properties, and the composition of soil microbial communities. Geoderma 2003, 114, 279–303. [Google Scholar] [CrossRef]
  95. Hamilton, T.L.; Boyd, E.S.; Peters, J.W. Environmental constraints underpin the distribution and phylogenetic diversity of nifH in the Yellowstone Geothermal Complex. Microb. Ecol. 2011, 61, 860–870. [Google Scholar] [CrossRef] [PubMed]
  96. Hayden, H.L.; Drake, J.; Imhof, M.; Oxley, A.P.A.; Norng, S.; Mele, P.M. The abundance of nitrogen cycle genes amoA and nifH depends on land-uses and soil types in South-Eastern Australia. Soil Biol. Biochem. 2010, 42, 1774–1783. [Google Scholar] [CrossRef]
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Figure 1. Soil physicochemical properties ((a) soil pH; (b) soil moisture; (c) soil electrical conductivity). Data (means ± SE; n = 3) with different lowercase letters indicate significant differences at 0.05 probability. Abbreviations: CK, control; Ni, nitrate; Am, ammonium; Ur, urea; Mix, mixed N; PL, monocultural P. laciniata; BP, monocultural B. pilosa; PLBP, co-cultivated B. pilosa and P. laciniata.
Figure 1. Soil physicochemical properties ((a) soil pH; (b) soil moisture; (c) soil electrical conductivity). Data (means ± SE; n = 3) with different lowercase letters indicate significant differences at 0.05 probability. Abbreviations: CK, control; Ni, nitrate; Am, ammonium; Ur, urea; Mix, mixed N; PL, monocultural P. laciniata; BP, monocultural B. pilosa; PLBP, co-cultivated B. pilosa and P. laciniata.
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Figure 2. Soil carbon and nitrogen contents ((a) total soil organic carbon content; (b) soil nitrate content; (c) soil ammonium content). Data (means ± SE; n = 3) with different lowercase letters indicate significant differences at 0.05 probability. Data (i.e., the contents of soil microbial carbon, total soil organic nitrogen, and soil microbial nitrogen) without significant differences (p > 0.05) among the different treatments were not shown in this figure. Abbreviations: CK, control; Ni, nitrate; Am, ammonium; Ur, urea; Mix, mixed N; PL, monocultural P. laciniata; BP, monocultural B. pilosa; PLBP, co-cultivated B. pilosa and P. laciniata.
Figure 2. Soil carbon and nitrogen contents ((a) total soil organic carbon content; (b) soil nitrate content; (c) soil ammonium content). Data (means ± SE; n = 3) with different lowercase letters indicate significant differences at 0.05 probability. Data (i.e., the contents of soil microbial carbon, total soil organic nitrogen, and soil microbial nitrogen) without significant differences (p > 0.05) among the different treatments were not shown in this figure. Abbreviations: CK, control; Ni, nitrate; Am, ammonium; Ur, urea; Mix, mixed N; PL, monocultural P. laciniata; BP, monocultural B. pilosa; PLBP, co-cultivated B. pilosa and P. laciniata.
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Microorganisms 12 01624 g003aMicroorganisms 12 01624 g003bMicroorganisms 12 01624 g003c
Figure 3. Soil enzymatic activities ((a) soil polyphenol oxidase activity; (b) soil cellulase activity; (c) soil β-glucosidase activity; (d) soil β-xylosidase activity; (e) soil FDA hydrolase activity; (f) soil sucrase activity; (g) soil protease activity; (h) soil urease activity). Data (means ± SE; n = 3) with different lowercase letters indicate significant differences at 0.05 probability. Abbreviations: CK, control; Ni, nitrate; Am, ammonium; Ur, urea; Mix, mixed N; PL, monocultural P. laciniata; BP, monocultural B. pilosa; PLBP, co-cultivated B. pilosa and P. laciniata.
Figure 3. Soil enzymatic activities ((a) soil polyphenol oxidase activity; (b) soil cellulase activity; (c) soil β-glucosidase activity; (d) soil β-xylosidase activity; (e) soil FDA hydrolase activity; (f) soil sucrase activity; (g) soil protease activity; (h) soil urease activity). Data (means ± SE; n = 3) with different lowercase letters indicate significant differences at 0.05 probability. Abbreviations: CK, control; Ni, nitrate; Am, ammonium; Ur, urea; Mix, mixed N; PL, monocultural P. laciniata; BP, monocultural B. pilosa; PLBP, co-cultivated B. pilosa and P. laciniata.
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Figure 4. SBC’s alpha diversity ((a) OTU’s species index; (b) Shannon’s diversity index; (c) Simpson’s dominance index; (d) Pielou’s evenness index; (e) Chao1’s richness index; (f) ACE’s richness index; (g) phylogenetic diversity index). Data (means ± SE; n = 3) with different lowercase letters indicate significant differences at 0.05 probability. Abbreviations: CK, control; Ni, nitrate; Am, ammonium; Ur, urea; Mix, mixed N; PL, monocultural P. laciniata; BP, monocultural B. pilosa; PLBP, co-cultivated B. pilosa and P. laciniata.
Figure 4. SBC’s alpha diversity ((a) OTU’s species index; (b) Shannon’s diversity index; (c) Simpson’s dominance index; (d) Pielou’s evenness index; (e) Chao1’s richness index; (f) ACE’s richness index; (g) phylogenetic diversity index). Data (means ± SE; n = 3) with different lowercase letters indicate significant differences at 0.05 probability. Abbreviations: CK, control; Ni, nitrate; Am, ammonium; Ur, urea; Mix, mixed N; PL, monocultural P. laciniata; BP, monocultural B. pilosa; PLBP, co-cultivated B. pilosa and P. laciniata.
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Figure 5. PCA of correlation patterns of the physicochemical properties, C and N contents, enzymatic activities in soil, and SBC’s alpha diversity. The X-axis and Y-axis account for 29.14% and 10.88% of the total variation, respectively. Abbreviations: SEC, soil electrical conductivity; TSOC, total soil organic carbon content; SMC, soil microbial carbon content; TSON, total soil organic nitrogen content; SMN, soil microbial nitrogen content; SNIT, soil nitrate content; SAMM, soil ammonium content; SPOL, soil polyphenol oxidase activity; SCEL, soil cellulase activity; SGLU, soil β-glucosidase activity; SXYL, soil β-xylosidase activity; SFDA, soil FDA hydrolase activity; SSUC, soil sucrase activity; SPRO, soil protease activity; SURE, soil urease activity; OTU, OTU’s species index; Shannon, Shannon’s diversity index; Simpson, Simpson’s dominance index; Pielou, Pielou’s evenness index; Chao, Chao1’s richness index; ACE, ACE’s richness index; PDI, phylogenetic diversity index.
Figure 5. PCA of correlation patterns of the physicochemical properties, C and N contents, enzymatic activities in soil, and SBC’s alpha diversity. The X-axis and Y-axis account for 29.14% and 10.88% of the total variation, respectively. Abbreviations: SEC, soil electrical conductivity; TSOC, total soil organic carbon content; SMC, soil microbial carbon content; TSON, total soil organic nitrogen content; SMN, soil microbial nitrogen content; SNIT, soil nitrate content; SAMM, soil ammonium content; SPOL, soil polyphenol oxidase activity; SCEL, soil cellulase activity; SGLU, soil β-glucosidase activity; SXYL, soil β-xylosidase activity; SFDA, soil FDA hydrolase activity; SSUC, soil sucrase activity; SPRO, soil protease activity; SURE, soil urease activity; OTU, OTU’s species index; Shannon, Shannon’s diversity index; Simpson, Simpson’s dominance index; Pielou, Pielou’s evenness index; Chao, Chao1’s richness index; ACE, ACE’s richness index; PDI, phylogenetic diversity index.
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Liu, Y.; Du, Y.; Li, Y.; Li, C.; Zhong, S.; Xu, Z.; Wang, C.; Du, D. Does Bidens pilosa L. Affect Carbon and Nitrogen Contents, Enzymatic Activities, and Bacterial Communities in Soil Treated with Different Forms of Nitrogen Deposition? Microorganisms 2024, 12, 1624. https://doi.org/10.3390/microorganisms12081624

AMA Style

Liu Y, Du Y, Li Y, Li C, Zhong S, Xu Z, Wang C, Du D. Does Bidens pilosa L. Affect Carbon and Nitrogen Contents, Enzymatic Activities, and Bacterial Communities in Soil Treated with Different Forms of Nitrogen Deposition? Microorganisms. 2024; 12(8):1624. https://doi.org/10.3390/microorganisms12081624

Chicago/Turabian Style

Liu, Yingsheng, Yizhuo Du, Yue Li, Chuang Li, Shanshan Zhong, Zhelun Xu, Congyan Wang, and Daolin Du. 2024. "Does Bidens pilosa L. Affect Carbon and Nitrogen Contents, Enzymatic Activities, and Bacterial Communities in Soil Treated with Different Forms of Nitrogen Deposition?" Microorganisms 12, no. 8: 1624. https://doi.org/10.3390/microorganisms12081624

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