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Article

Effects of Urban Forest Types and Traits on Soil Organic Carbon Stock in Beijing

by
Xinhui Xu
1,2,
Zhenkai Sun
1,2,*,
Zezhou Hao
1,2,
Qi Bian
1,2,
Kaiyue Wei
1,2 and
Cheng Wang
1,2
1
Research Institute of Forestry, Chinese Academy of Forestry, Beijing 100091, China
2
Key Laboratory of Tree Breeding and Cultivation and Urban Forest Research Centre, National Forestry and Grassland Administration, Beijing 100091, China
*
Author to whom correspondence should be addressed.
Forests 2021, 12(4), 394; https://doi.org/10.3390/f12040394
Submission received: 13 February 2021 / Revised: 12 March 2021 / Accepted: 24 March 2021 / Published: 26 March 2021
(This article belongs to the Section Forest Ecology and Management)
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Abstract

:
Forests can affect soil organic carbon (SOC) quality and distribution through forest types and traits. However, much less is known about the influence of urban forests on SOC, especially in the effects of different forest types, such as coniferous and broadleaved forests. Our objectives were to assess the effects of urban forest types on the variability of SOC content (SOC concentration (SOCC) and SOC density (SOCD)) and determine the key forest traits influencing SOC. Data from 168 urban forest plots of coniferous or broadleaved forests located in the Beijing urban area were used to predict the effects of forest types and traits on SOC in three different soil layers, 0–10 cm, 10–20 cm, and 20–30 cm. The analysis of variance and multiple comparisons were used to test the differences in SOC between forest types or layers. Partial least squares regression (PLSR) was used to explain the influence of forest traits on SOC and select the significant predictors. Our results showed that in urban forests, the SOCC and SOCD values of the coniferous forest group were both significantly higher than those of the broadleaved group. The SOCC of the surface soil was significantly higher than those of the following two deep layers. In PLSR models, 42.07% of the SOCC variance and 35.83% of the SOCD variance were explained by forest traits. Diameter at breast height was selected as the best predictor variable by comparing variable importance in projection (VIP) scores in the models. The results suggest that forest types and traits could be used as an optional approach to assess the organic carbon stock in urban forest soils. This study found substantial effects of urban forest types and traits on soil organic carbon sequestration, which provides important data support for urban forest planning and management.

1. Introduction

Urban green spaces, including urban forests, play a pivotal role as substitutes for the lost natural environment in the city’s original location [1]. Urban forests provide a large number of ecosystem services [2], such as enhancing amenity values [3], maintaining biodiversity [4], and increasing carbon sequestration [5]. The increase and decrease of soil organic carbon (SOC) may affect climate change greatly [6,7]. Moreover, SOC storage impacts the other ecological functions of soil as well, such as biomass production, nutrient and water-holding capacity, infiltration capacity and resistance to erosion, and providing habitats for biological activity [8,9]. Studies of forest groups and species characteristics affecting soil fertility parameters have been widely carried out in the non-urban environment [10], but less so in an urban context [11]. An in-depth understanding of the relationship between urban forest and SOC is key to maintain and enhance the quality of urban ecosystem services.
There is growing recognition of the top-down and bottom-up regulation between plants and soil organisms [12]. Studies of the effects of aboveground forest types and traits on SOC distribution are also underway. Jobbagy and Jackson (2000) found that different forest types significantly affected the vertical distribution of SOC [13]. There is generally high variability in urban SOC, and Canedoli et al. (2019) showed that the SOC concentration (SOCC) of urban parks was higher than that of non-parks, defined as green squares, private gardens, tree lines, or street greens [14]. In an urban context, soils are not only under the disturbance of an artificial environment but are also affected by vegetation [15]. Urban trees can affect the soil’s biological, physical, and chemical properties through their root systems and the quantity and quality of fallen leaves [16]. Understanding the impact of urban trees on soil properties is critical [17]. However, the effect of urban forests on SOC and to what extent urban forests can increase SOC reserves remain unclear.
It has been long recognized that forest types differ greatly in forest traits [18] and thereby can affect ecosystem properties, including soil organic matter [5]. The previous studies of forest traits in relation to soil carbon stocks have focused on some key factors, such as tree canopy [19], diameter at breast height [20,21], litterfall [22,23,24], fine root biomass [25], and herbaceous vegetation [26]. These forest traits affect SOC and other soil properties through direct or indirect pathways. The direct pathway of trees interacting with soil includes both leaf litter input and root release. The litterfall from woody plants is the main source of soil organic matter [27,28,29,30,31]. Tree species vary significantly in their litter quality, as well as in their litter decomposition rates [32]. In the urban environment, the litter disposal methods of different forest types may influence soil organic carbon differently. The low crown and needle leaves of coniferous species mean that their fallen leaves are cleaned up less often [33,34], whereas the fallen leaves of deciduous broad-leaved forests are often cleaned up. Experiments have demonstrated that tree roots release substantial quantities of carbon into soil [35,36]. An indirect pathway by which forests interact with SOC—whereby forests or a single tree may affect soil respiration—is providing a microenvironment and microclimate for the soil. Thereby, urban forest types and tree species may impact soil organization and related process through the microenvironment, litterfall, and tree roots, thereby leading to differences in urban forest SOC.
So far, Beijing has implemented two rounds of the Million-Mu (667 m2) Plain Afforestation Project. In recent years, Beijing’s urban forest afforestation area is constantly increasing, which provided good conditions for the development of this study [37,38]. Currently, the connections between urban forest and soil organic carbon stock are still under-explored. To help address these knowledge gaps, we studied 107 urban parks in Beijing. Based on SOC stock and urban forest types and traits, we hypothesized that: (1) urban forest soil organic carbon is different between coniferous and broadleaved forests, (2) urban forest traits have a significant influence on soil organic carbon, and (3) soil organic carbon in different layers has a different relationship with urban forest traits. In this study, we aimed to elucidate the relationship between urban forest and soil organic carbon so as to provide data support for urban forest planning and management in the future.

2. Study Area and Methods

2.1. Study Area

Beijing, the capital city of China, has a history of over 3000 years. Over the past decades, Beijing has been undergoing rapid development, and a series of ring roads were constructed as the city expanded outward from its historic center. This urbanization occurred in all four directions, started from the central area inside the 2nd ring road, then sequentially toward the surrounding areas [39]. The study area was all within the sixth ring road, which covers the central and suburban areas of Beijing (Figure 1).
Based on maps and reachable park directories on the Baidu Map, we located over 200 parks on the map. With the map gridded by 5 km × 5 km, we randomly selected one park in each grid. We discarded parks that were built on former factories to ensure that they were only affected by the typical urban forest environment. After this, we manually added some parks more than 50 years old to make the age of parks more even. Then, 107 parks were selected in total. We tried to sample both coniferous and broadleaved forests in each park to compare the SOC content between forest types. Finally, we sampled 168 plots, which contained 99 broadleaved and 69 coniferous plots. There were 61 parks with both coniferous and broadleaved forest types. The information on sampling sites and species is displayed in Appendix A, Table A1.
We followed five principles to select the sampling plots in parks. Firstly, the plots were set more than 5 m away from the walking path and 20 m away from the traffic artery. Secondly, the plot’s understory vegetation was stable and was not to be changed every year to avoid large soil disturbances. Thirdly, plots were selected that were not watered within three days to reduce the short-term impact of human management. Fourthly, the plot’s size was required to be bigger than 10 m × 10 m. The sizes of plots ranged from 100 m2 (10 m × 10 m) to 225 m2 (15 m × 15 m) in this study. Fifthly, monocultures were sampled to focus on the effects of tree species on SOC. The monocultures were composed of common tree species in Beijing and were artificial single communities.

2.2. Methods

2.2.1. Soil Sampling and Vegetation Investigation

Soil was sampled in September and October 2018 at the edge of the canopy projection, so the distance to the nearest tree trunk ranged from 1.2 m to 10 m, with an average distance of 4 m from the trunk [40,41]. At each sampling point, we removed the litter layer and collected samples by using a steel push corer with a 3.8-cm inner diameter and a length of 20 cm (Soil Sampler; Hongguang Instrument Inc., Shaoxing, China) to obtain three layers of 0–10 cm, 10–20 cm, and 20–30 cm samples [41,42]. Six samples distributed evenly in each plot were sampled for each vertical soil layer. The soil samples were mixed and transported in a cooler to the laboratory for further analyses.
We investigated the vegetation density (VD) of trees, tree height (H), under crown height (UC), diameter at breast height (DBH, 1.30 m above the ground level), leaf area index (LAI), canopy density (CD), fine root biomass (FRB), canopy area (CA), herbaceous vegetation cover (HB), and semi-decomposed litter (LIT) as forest traits. LAI was measured with an LAI-2200C plant canopy analyzer (LI-COR Inc., Lincoln, NE, USA), following the method as described in the study by Thimonier et al. [43]. Plant density of trees was calculated using the number of trees divided by the area of the sample plot. In the herb survey, 5 small subplots of 1 m × 1 m were selected, and the herbaceous vegetation cover and herbaceous species were measured in the small samples. We also collected fine roots of three soil layers in each plot and collected three 10 cm × 10 cm frames of litter samples in each plot to obtain the fine root biomass and semi-decomposed litter quantity. Root samples were collected with the steel corer mentioned above. Soil samples with roots were labeled and put into 1-mm mesh nylon bags and we used a flotation method to separate the roots from the soil [44,45]. The nylon bags were soaked in fresh water for 12 h and washed under regular running water to obtain clean roots [46]. Fine roots were divided as those with a diameter less than 2 mm, based on the cleaned roots. We further differentiated live roots from dead roots based on the shape, color, xylem, and elasticity of the roots and eliminated the roots of shrubs and herbs. Fine root samples were dried at 65 °C until the mass was constant and weighed with an electronic balance (±0.0001 g). We obtained the fine root biomass (g/m3) by dividing the fine root weight by the soil sample volume. The semi-decomposed litter samples were dried to a constant weight at 65 °C and weighed [47]. We used another set of tools to dig the complete core samples to calculate soil moisture content (SMC) and soil bulk density (BD). This set of tools was specially designed for study areas which could not be dug up for soil profiles. The set contains a fixed sleeve in which the ring knife can be put in and used to take intact soil samples.

2.2.2. Soil Preparation and Analysis

We analyzed the soil moisture content (SMC), soil pH, soil bulk density (BD), soil organic matter concentration (SOCC), and density (SOCD). In brief, all laboratory tests followed standard methods. SMC was determined by gravimetric methods. To measure soil pH, water and field-moist soil were mixed in a 1:1 volumetric ratio, allowed to stand for 10 min, and pH was then estimated in the supernatant using a bench-top pH meter, reflecting the soil acidity. To test BD, the intact soil cores were dried at a temperature of 105 °C and soil BD was obtained by dividing the dry soil weight by the volume of the intact soil core (100 cm3). The SOCC (g kg−1) was measured using a SOC analyzer (Multi N/C 3100, Analytik, Jena, Germany). SOCD (kg m−2) within each sample was calculated according to Equation [48]:
SOCD = BD × SOC × h
where BD is the bulk density (g/cm3), SOC is the soil organic carbon content (g/kg), and h is the depth of each soil layer (0.1 m).

2.3. Statistical Analyses

In this study, statistical analyses were performed using the statistical software R 4.0.3 (R Core Team, 2016) to reveal the relationships between the urban forest and soil variables. All datasets were checked for normality using the Shapiro–Wilk test (p > 0.05) prior to analysis and then normalized or scaled if necessary.
Soil parameter differences between the two forest types (coniferous and broadleaved) in three layers (0–10 cm, 10–20 cm, and 20–30 cm) were tested by two-way ANOVA, whereas no interaction effect was found in this study. Therefore, a one-way ANOVA test was separately performed on forest types and layers. The Levene test was performed to test the homogeneity of variance. The Kruskal–Wallis test was performed on pH and SMC values as these data failed for normality, and other soil variables (SOCC, SOCD, and BD) were analyzed using the parameter approach. The Steel–Dwass test and the Tukey HSD (honest significant difference) post-hoc tests were used to analyze differences among three layers.
Partial least squares regression (PLSR) was used to evaluate the influence of forest traits on SOCC and SOCD. PLSR integrates the advantages of principal component analysis (PCA), canonical correlation analysis (CCA), and multiple linear regression. PLSR has been widely applied to the study of forest ecosystems and has been proven to reveal the relationship between environmental factors and forest structure. In PLSR, forest traits and soil variables were chosen as predictors. Ten forest traits and three soil variables were chosen as predictor variables for PLSR—H, FRB, LAI, HC, LIT, VD, UC, CD, soil pH, soil moisture content, and bulk density. SOCC and SOCD were chosen as response variables. All variables were inspected for outliers before modeling. Leave-one-out cross-validation was used to select the optimum number of components. The root mean squared error of prediction (RMSEP) and the coefficient of determination (R2) were used to evaluate the model’s performance. Variable importance in projection (VIP) scores were used to evaluate the predictors’ contribution to PLSR [49]. Predictors with VIP scores greater than 1 were considered important to the models. The R packages ‘pls’ and ‘plsVarSel’ were used to perform the analyses.

3. Results

3.1. Variance of Soil Properties under Urban Forests

The soil organic carbon of urban forests varied significantly. The average value of SOCC and SOCD across all the parks was 8.02 ± 0.12 g kg−1 (mean ± standard error) and 1.21 ± 0.02 kg m−2 (mean ± standard error), respectively (Table 1). SOCC showed significant difference between forest types (F-value = 6.556, p < 0.05) and so did SOCD (F-value = 5.264, p < 0.05). Soils under coniferous trees had higher SOCC and SOCD than those under broadleaved trees (Table 1). There was a significant difference in SOCC (p < 0.01) among different layers but not in SOCD. According to multiple comparisons, the 0–10 cm layer held significantly higher SOCC than both the 10–20 cm and 20–30 cm layers. Bulk density (1.53 ± 0.19 g cm−3) and pH (7.82 ± 0.55) showed no significant difference between the coniferous and broadleaved plant groups (p > 0.05). SMC (12 ± 5%) was significantly different between these two forest types. The soil under coniferous trees was moister than that under broadleaved trees. There were significant differences among the three layers only in BD.

3.2. Variance of Forest Traits

The results showed that two popular families, Salicaceae and Pinaceae, dominated the forests. The Wilcoxon test for paired samples was performed to identify the differences in forest traits between plant groups. There were significant differences in forest traits between coniferous and broadleaved groups (Figure 2). The results showed that there were significant differences in most forest traits between the two forest types. Among them, LAI, FRB, VD, HB, and CD values were significantly higher in coniferous forests. In contrast, H, UC, DBH and CA were significantly higher in broadleaved trees. Meanwhile, the semi-decomposed litter quantity showed no significant difference between forest types, which may be due to clearing and leaf management in parks.

3.3. Effect of Forest Traits on SOC

The performance of the PLSR models is shown in Table 2. For the total SOCC and SOCD models, higher R2 and lower RMSEP values were observed in the total SOCC model. In the total SOCC model, the components explained 42.07% of the variance in SOCC; in the 10–20 cm model, the components explained 45.50% of the variance in SOCC, which was the highest level of explanation among the three layers. In the total SOCD model, the components explained 35.83% of the variance in SOCD; in the 10–20 cm model, the components explained 45.83%. These results showed that forest traits had a more substantial explanatory power for total SOCC. Simultaneously, three components were observed in both the best performing SOCC and SOCD models, and the addition of more components did not improve the explanatory power of the model. The following components did not have a strong correlation with the residuals of the predictors. Different models in different layers analysis showed that forest traits had more substantial explanatory power for the SOCC and SOCD models at a depth of 10–20 cm. In comparison, the explanatory power for the 0–10 cm and 20–30 cm models was slightly weaker than that of the 10–20 cm model.
Concerning the VIP scores of each of the forest traits, DBH had an important contribution in all models (Table 3). The traits of LAI, DBH, CA, HC, and CD showed important contributions to the models of both the total SOCC and SOCD, indicating that forest traits associated with forest biomass had a strong relationship with SOC in urban forests. Moreover, comparing the results of different layer models showed that more forest traits contributed to the SOCC and SOCD models at the 10–20 cm layer than the other two layers. FRB’s VIP score was greater than 1 only in the 10–20 cm layer model, which showed a relationship between forest fine roots and SOCC and SOCD in urban forests. The contribution of forest traits was the least in the 0–10 cm model. Additionally, based on the regression coefficient of each forest trait, it was found that except for the weak negative correlation coefficient between CA and SOC in the 0–10 cm layer model, the other forest traits positively correlated with SOC. The VIP scores of LIT, VD, and UC in all models were less than 1. The results showed that these three forest traits had no statistically significant relationships with SOCC and SOCD in urban forests. Overall, these results showed that forest traits positively affected SOCC and SOCD in urban forests.

4. Discussion

Our results showed that the coniferous and broadleaved urban forest groups significantly affected soil organic carbon. Specifically, SOCC and SOCD were higher in the coniferous group than in the broadleaved group. This result is similar to findings in a natural context by Błońska and Gruba [50] and findings in urban parks in Finland by Setälä et al. [41]. Here, even in an urban context, SOC of the coniferous type forest was higher than that of the broadleaved forest, similar to forest communities in natural ecosystems—for instance, the carbon concentration under a spruce forest was found to be higher than under broadleaves [51,52]. This trend in SOC content of different forest types may be because conifers have a higher leaf area index, even though broadleaved trees have larger crowns. Our result is similar to Bae and Ryu’s findings that complex canopy structure may boost organic carbon in forest soils [53]. The FRB of coniferous trees is also higher than that of broadleaved trees, and fine roots are another factor that directly affects soil organic carbon [54]. Some studies on urban forest roots have revealed that the roots of urban trees can maintain or enhance organic matter in soil [55]. In the three soil layers, SOCC in 0–10 cm was significantly higher than the other two layers, whereas there was no difference in SOCD among layers. Edmondson reported similar results, demonstrating that not only SOCC but also SOCD of urban forest differed among different layers [17]. In our study, the top layer in the coniferous group held the highest SOCC (Table 1). Due to the input of nutrients from vegetation and artificial management, the content of organic carbon in the surface layer of soil is usually high, which exhibits a dynamic interaction with biological and anthropogenic activities [56,57]. Therefore, in cities, soils under coniferous trees, especially the upper layer, can provide greater potential for organic carbon storage.
The PLSR of SOCC and SOCD models selected significant variables with VIP scores > 1. DBH was the only variable in all models showing VIP > 1 and the highest VIP, which indicated that DBH was the most important predictor for SOC content in our study. Our result is similar to the study of Eni, which found that DBH was the only canonical variable revealing soil-vegetation interrelationships [58]. In the two forest types, the DBH of broadleaves was higher than that of conifers, whereas the soil organic carbon under broadleaves was lower than that of conifers. Moreover, the result of PLSR showed that there was a positive correlation between DBH and SOCC. This means that the difference in coniferous and broadleaved forest soil organic carbon is likely to be caused by many factors. Moreover, we found that all variables of crown characteristics—LAI, canopy area, and canopy density—were also important for the prediction of urban forest soil organic carbon, with VIP scores > 1 in at least seven models (Table 3). Thus, the results indicate that the canopy structure of urban forest communities has an important impact on soil organic carbon. The difference in forest traits among forest types showed that the LAI and canopy density of conifers were higher than those of broadleaved trees, whereas canopy area displayed the opposite result. These results, combined with the PLSR results, may emphasize that LAI and canopy density have a stronger effect on soil organic carbon and are more suitable to be predictors. On the one hand, a complete and complex canopy structure in urban forests can increase the input of litter in the area, which becomes an important source for accumulating organic carbon in the soil [59]. According to the significant difference between forest types in the leaf area index and the lack of differences between them in litter, we can infer that human activities strongly influence this mechanism, such as litter removal through management practices [60,61,62]. On the other hand, changes in canopy structure affect the microclimate of the soil habitat, including environmental factors such as temperature, light, wind speed, and precipitation [63]. The environments of forests can affect the activities of fauna and organisms in the soil [64,65], thus changing the overall soil respiration intensity and affecting the decomposition and transformation of soil organic carbon [66]. Based on the models of total SOCC and SOCD, the forest traits mentioned showed a positive correlation with urban soil organic carbon. This positive correlation revealed a correlation between tree biomass and soil organic carbon content, suggesting that urban forests with more complex canopies and higher leaf areas may have higher organic carbon stock in their soils. In addition, our results also showed that forest type did not account for all variance in SOC, indicating that more factors need to be taken into account, such as urban forest age and position. Many studies have shown that urban forest age has a positive effect on SOC and SOC [11,67,68]. Habitats with a more mature and stable urban forest structure can provide good shelter and necessary food sources for aboveground organisms [68] and play a positive role in the underground ecological environment [21].
In addition, we used forest traits to predict the overall SOCC and SOCD and studied the relationship between SOC content and forest traits at different soil layers. The results showed that SOC content in 10–20 cm layer was most closely related to forest traits, with the highest model interpretation and stability (Table 2). Notably, the VIP score of fine root biomass was greater than 1 in the models both of SOCC and SOCD in the 10–20 cm layer, which indicated the contribution of fine roots to soil organic carbon in this layer. Huyler et al. also found that tree roots played a role in maintaining the carbon level below the soil surface [69]. Fine roots are important plant organs used to absorb water and nutrients [70], and fine roots are analogous to leaves and central organic matter inputs, given that the sloughed roots are added to the soil humus pool [68]. Due to the rapid renewal of fine roots, the annual return of carbon, nutrients, and energy from fine roots to the soil is even higher than that of ground litter [71], which was confirmed by the study of Hui et al. [72]. At 0–10 cm, the models showed that the contribution of forest traits to SOC content was the weakest. The contribution of litter content to SOC was not found in any model, which indicates that the organic carbon in urban forest soil was affected by other factors than litter input in our study. This study’s sampling area was concentrated in urban parks, and the sampling area was disturbed by human factors to varying degrees. At present, most of the litter management in parks in Beijing area is still dominated by regular cleaning, which leads to the litter being cleared away and degrading soil organic carbon. The high-intensity manual management pattern in urban parks destroys surface soil structure and accelerates the decomposition of organic carbon and therefore SOC cannot accumulate effectively [73,74]. In contrast, green space management in Paris may help to increase SOC stock in open soil [75]. However, researchers of urban forest soil organic carbon need to learn more from the research experience of natural forest soil and carry out more systematic and comprehensive research in the world [76].

5. Conclusions

A better understanding of the effects of urban forests on SOC content is crucial to advancing urban ecosystem services, even though quantifying and predicting carbon in urban forest soil remains difficult. Thus, our results demonstrated that urban forests affect the concentration and density of soil organic carbon through forest types and forest traits in temperate climates. We found that there was a significant difference in SOC content between coniferous and broadleaved types in urban forests in Beijing. Using PLSR, we selected diameter at breast height, leaf area index, crown area, and canopy density as the significant predictors of soil organic carbon in urban forests. The data show that analyzing forest traits could be an optional approach for cost-effectively predicting urban forest SOC with higher accuracy and practicability.

Author Contributions

Conceptualization, X.X., C.W. and Z.S.; investigation, X.X., Z.H., Q.B. and K.W.; writing—original draft, X.X.; writing—review and editing, Z.S. and Z.H. All authors have read and agreed to the published version of the manuscript.

Funding

This work was funded by National Non-Profit Research Institutions of the Chinese Academy of Forestry (grant numbers: CAFYBB2020ZB008) and by the China Scholarship Council (CSC) (grant numbers: 201903270038).

Acknowledgments

We truly appreciate Susan Day for her guidance and thoughtful suggestions.

Conflicts of Interest

The authors declare no conflict of interest.

Appendix A

Table
Table A1. List of sampling park names, sizes, ages, tree species, and locations.
Table A1. List of sampling park names, sizes, ages, tree species, and locations.
NumberPark NameSize (ha)Age (Year)SpeciesLocation of Ring Road
ConiferBroadleaf
1Dongfutougou Park24 8-Salix matsudana Koidz.5 to 6
2Zhongguancun forest Park340 14Pinus tabuliformis Carr.Ailanthus altissima (Mill.) Swingle 5 to 6
3Spring Park11 12-Ginkgo biloba L.5 to 6
4Dongxiaoying Park1 8-Salix matsudana5 to 6
5Baiwang Park9 12-Ginkgo biloba5 to 6
6Mingyuan Park3 3Juniperus chinensis Linn. Euonymus maackii Rupr. 5 to 6
7Riveside forest Park431 8Cedrus deodara (Roxburgh) G. Don Platanus occidentalis L. 5 to 6
8Huilongyuan 10 20Metasequoia glyptostroboides Hu et W. C. Cheng Sophora japonica L. 5 to 6
9Bishuifenghe 3 28Pinus bungeana Zucc. et Endi Sophora japonica5 to 6
10Zhenggezhuang Park1 13-Populus tomentosa Carr. 5 to 6
11Haiyingluo Park74 5Pinus bungeanaSalix matsudana5 to 6
12Future technolgy Park314 5-Fraxinus chinensis Roxb.5 to 6
13Banta country Park42 5Juniperus formosanaPopulus tomentosa5 to 6
14Taiping country Park43 11-Populus tomentosa5 to 6
15Huabohui thesis Park27 20-Populus tomentosa5 to 6
16Hedi Park2 6Pinus tabuliformisFraxinus chinensis5 to 6
17Mananli Park2 25-Sophora japonica5 to 6
18Yongshiying country Park21 8Pinus tabuliformisSalix matsudana5 to 6
19Olympic Forest Park624 11Pinus tabuliformisAilanthus altissima4 to 5
20Heiqiao Park138 15-Populus tomentosa5 to 6
21Yujin Park17 15Juniperus formosana-5 to 6
22Riverside Park1 5Pinus tabuliformisSophora japonica5 to 6
23Yuwen river Park16 4Pinus tabuliformisSalix matsudana5 to 6
24Dongba country Park234 10-Salix matsudana5 to 6
25Entertainment sport Park7 8-Salix matsudana4 to 5
26Baliqiao music Park17 10Pinus tabuliformisSalix matsudana5 to 6
27Longwangzhuang Park4 9-Sophora japonica5 to 6
28Taihu forest Park76 5Pinus tabuliformisRobinia pseudoacacia L. 5 to 6
29Dongshi Park20 3-Fraxinus chinensis5 to 6
30Lvfeng Park23 5Pinus tabuliformisSophora japonica5 to 6
31Nanhaizi Park432 9Pinus tabuliformisPlatanus acerifolia (Aiton) Willdenow 5 to 6
32Boda Park16 15Pinus tabuliformisEucommia ulmoides Oliver 5 to 6
33Binhe Park312 2-Salix matsudana5 to 6
34Yizhuang Park6 4Pinus tabuliformisSalix matsudana5 to 6
35Laojuntang Park47 11-Populus tomentosa4 to 5
36Huangcun Park5 35Juniperus formosana-5 to 6
37Qingyuan Park124 10Platycladus orientalis (L.) Franco Fraxinus chinensis5 to 6
38Gaoxin Park42 10Platycladus orientalisSalix matsudana4 to 5
39Yukang Park40 11Pinus tabuliformisSalix matsudana4 to 5
40Kandan Park49 10-Robinia pseudoacacia4 to 5
41Century Forest Park405 11Juniperus chinensisSophora japonica5 to 6
42Riverside Park312 16Pinus tabuliformisSalix matsudana5 to 6
43Huangxinzhuang Green Fitness Park6 10-Populus tomentosa5 to 6
44University Town Park6 6-Populus tomentosa5 to 6
45Changyang Park10 15Pinus tabuliformisPlatanus orientalis5 to 6
46Changti Park1 11-Koelreuteria paniculata Laxm. 5 to 6
47Changxindian Park8 32Juniperus formosanaKoelreuteria paniculata5 to 6
48Xiaoyue country Park37 10Juniperus formosanaSophora japonica5 to 6
49Guozhuang Park9 20Pinus bungeanaSalix matsudana4 to 5
50Small Park1 20Platycladus orientalisSophora japonica4 to 5
51Fengtai Science and Technology Park5 22-Koelreuteria paniculata3 to 4
52Fengtai Garden8 30-Koelreuteria paniculata3 to 4
53Wanfeng Park24 23Platycladus orientalisGinkgo biloba3 to 4
54Wukesong Cultural Park8 30Pinus tabuliformisSalix matsudana3 to 4
55Hope Park9 15Juniperus chinensisPopulus tomentosa5 to 6
56Ancient City Park14 38Pinus tabuliformisGinkgo biloba5 to 6
57Pine Forest Park22 70Platycladus orientalis-5 to 6
58Half-moon popular science garden3 20Pinus tabuliformisKoelreuteria paniculata4 to 5
59Laoshan City Leisure Park91 11Juniperus formosana HayataSalix matsudana4 to 5
60Sunshine Wednesday6 16-Salix matsudana4 to 5
61Pingzhuang country Park44 10-Ginkgo biloba4 to 5
62Beijing Botanical Garden400 63Pinus tabuliformisSalix matsudana5 to 6
63Chinese Academy of Sciences Botanical Garden74 89Juniperus chinensisPopulus tomentosa5 to 6
64Yudong Garden75 11Juniperus formosanaGinkgo biloba4 to 5
65Haidian Park 40 16-Sophora japonica4 to 5
66Shuangyushu Park1 34Juniperus formosanaSophora japonica3 to 4
67Dongsheng Bajia Country Park101 12-Salix matsudana4 to 5
68Zhiyuanzhuang Park12 6Juniperus formosanaFraxinus chinensis5 to 6
69International Camping Park replacement36 16Pinus bungeanaSophora japonica4 to 5
70Nanyuan Park13 70Juniperus formosanaPopulus tomentosa4 to 5
71Taoyuan Park11 18Juniperus formosanaSophora japonica4 to 5
72Wanfang Pavilion8 29-Sophora japonica2 to 3
73Fengyi Park10 15-Populus tomentosa2 to 3
74Bihai Park20 16Pinus tabuliformisKoelreuteria paniculata4 to 5
75Breeze Garden1 22Juniperus chinensisSalix matsudana3 to 4
76Haitang Park34 11Juniperus chinensisRobinia pseudoacacia4 to 5
77Guta Park56 11Pinus tabuliformisSophora japonica4 to 5
78Xinglong Park49 27Juniperus chinensis-4 to 5
79Ditan Park 35 479Platycladus orientalisSalix matsudana2 to 3
80Nanguan Park3 63-Sophora japonica1 to 2
81Xiangheyuan Park7 33-Sophora japonica2 to 3
82Side Park17 21Pinus tabuliformisKoelreuteria paniculata4 to 5
83Wanghe Park37 4Pinus tabuliformisFraxinus chinensis4 to 5
84Wong Tsao Wan Country Park39 10Pinus tabuliformisFraxinus chinensis4 to 5
85Zizhuyuan47 66Pinus bungeanaTilia tuan Szyszyl. 2 to 3
86Linglong Park9 30-Robinia pseudoacacia3 to 4
87Huichengmen Park3 50Juniperus chinensisPopulus tomentosa2 to 3
88Cuifang Garden1 29Pinus tabuliformis-1 to 2
89Nanlishi Road Park2 59Juniperus chinensisSophora japonica2 to 3
90Yuetan Park8 479Juniperus formosanaEuonymus maackii2 to 3
91Guanyuan Park2 19-Koelreuteria paniculata1 to 2
92Longtan Lake Park120 9Pinus tabuliformis-1 to 2
93Ritan Park21 479Platycladus orientalisEuonymus maackii2 to 3
94Tuanjie Lake Park13 33Juniperus formosana-3 to 4
95Red scarf Park24 61Juniperus chinensisGinkgo biloba4 to 5
96Chaoyang Park 210 35Pinus tabuliformisPopulus tomentosa3 to 4
97Taoranting Park55 67Juniperus chinensisSophora japonica1 to 2
98Dongdan Park4 70-Ginkgo biloba1 to 2
99Huangchenggen Heritage Park8 18-Ginkgo biloba1 to 2
100Jingshan Park 19 101Juniperus chinensis-1 to 2
101Xitucheng Park18 13-Sophora japonica2 to 3
102Rending Lake Park9 71-Ginkgo biloba2 to 3
103Rose Garden1 16Platycladus orientalisAilanthus altissima3 to 4
104Madian Park8 16Pinus tabuliformisGinkgo biloba3 to 4
105Arctic Temple Park5 6Pinus tabuliformisUlmus pumila L. 3 to 4
106Xinglong Park49 27-Sophora japonica4 to 5
107Xiangheyuan Park7 33Juniperus chinensis-2 to 3

References

  1. Francini, G.; Hui, N.; Jumpponen, A.; Kotze, D.J.; Romantschuk, M.; Allen, J.A.; Setälä, H. Soil biota in boreal urban greenspace: Responses to plant type and age. Soil Biol. Biochem. 2018, 118, 145–155. [Google Scholar] [CrossRef] [Green Version]
  2. Bolund, P.; Hunhammar, S. Ecosystem services in urban areas. Ecol. Econ. 1999, 29, 293–301. [Google Scholar] [CrossRef]
  3. Pandit, R.; Polyakov, M.; Tapsuwan, S.; Moran, T. The effect of street trees on property value in Perth, Western Australia. Landsc. Urban Plan. 2013, 110, 134–142. [Google Scholar] [CrossRef]
  4. Llausàs, A.; Roe, M. Green Infrastructure Planning: Cross-National Analysis between the North East of England (UK) and Catalonia (Spain). Eur. Plan. Stud. 2012, 20, 641–663. [Google Scholar] [CrossRef]
  5. Roeland, S.; Moretti, M.; Amorim, J.H.; Branquinho, C.; Fares, S.; Morelli, F.; Niinemets, Ü.; Paoletti, E.; Pinho, P.; Sgrigna, G.; et al. Towards an integrative approach to evaluate the environmental ecosystem services provided by urban forest. J. For. Res. 2019, 30, 1981–1996. [Google Scholar] [CrossRef] [Green Version]
  6. Lal, R. Residue management, conservation tillage and soil restoration for mitigating greenhouse effect by CO2-enrichment. Soil Tillage Res. 1997, 43, 81–107. [Google Scholar] [CrossRef]
  7. Schmidt, M.W.I.; Torn, M.S.; Abiven, S.; Dittmar, T.; Guggenberger, G.; Janssens, I.A.; Kleber, M.; Kögel-Knabner, I.; Lehmann, J.; Manning, D.A.C.; et al. Persistence of soil organic matter as an ecosystem property. Nature 2011, 478, 49–56. [Google Scholar] [CrossRef] [Green Version]
  8. Wiesmeier, M.; Urbanski, L.; Hobley, E.; Lang, B.; von Lützow, M.; Marin-Spiotta, E.; van Wesemael, B.; Rabot, E.; Ließ, M.; Garcia-Franco, N.; et al. Soil organic carbon storage as a key function of soils—A review of drivers and indicators at various scales. Geoderma 2019, 333, 149–162. [Google Scholar] [CrossRef]
  9. Lorenz, K.; Lal, R. Biogeochemical C and N cycles in urban soils. Environ. Int. 2009, 35, 1–8. [Google Scholar] [CrossRef]
  10. Lukina, N.V.; Tikhonova, E.V.; Danilova, M.A.; Bakhmet, O.N.; Kryshen, A.M.; Tebenkova, D.N.; Kuznetsova, A.I.; Smirnov, V.E.; Braslavskaya, T.Y.; Gornov, A.V.; et al. Associations between forest vegetation and the fertility of soil organic horizons in northwestern Russia. For. Ecosyst. 2019, 6, 1–19. [Google Scholar] [CrossRef] [Green Version]
  11. Liu, R.; Wang, M.; Chen, W. The influence of urbanization on organic carbon sequestration and cycling in soils of Beijing. Landsc. Urban Plan. 2018, 169, 241–249. [Google Scholar] [CrossRef]
  12. Bardgett, R.D.; Wardle, D.A. Aboveground-Belowground Linkages: Biotic Interactions, Ecosystem Processes, and Global Change; Oxford University Press: Oxford, UK, 2010; ISBN 0199546878. [Google Scholar]
  13. Jobbagy, E.G.; Jackson, R.B. The Vertical Distribution of Soil Organic Carbon and Its Relation to Climate and Vegetation. Ecol. Appl. 2000, 10, 423. [Google Scholar] [CrossRef]
  14. Canedoli, C.; Ferrè, C.; El Khair, D.A.; Padoa-Schioppa, E.; Comolli, R. Soil organic carbon stock in different urban land uses: High stock evidence in urban parks. Urban Ecosyst. 2020, 23, 159–171. [Google Scholar] [CrossRef]
  15. Reichert, B.L.; Jean-Philippe, S.R.; Oswalt, C.; Franklin, J.; Radosevich, M. Woody Vegetation and Soil Characteristics of Residential Forest Patches and Open Spaces along an Urban-to-Rural Gradient. Open J. For. 2015, 5, 90–104. [Google Scholar] [CrossRef] [Green Version]
  16. Day, S.D.; Wiseman, P.E.; Dickinson, S.B.; Harris, J.R. Tree root ecology in the Urban environment and implications for a sustainable rhizosphere. Arboric. Urban For. 2010, 36, 193–205. [Google Scholar]
  17. Edmondson, J.L.; O’Sullivan, O.S.; Inger, R.; Potter, J.; McHugh, N.; Gaston, K.J.; Leake, J.R. Urban tree effects on soil organic carbon. PLoS ONE 2014, 9. [Google Scholar] [CrossRef] [Green Version]
  18. Grime, J.P. Evidence for the Existence of Three Primary Strategies in Plants and Its Relevance to Ecological and Evolutionary Theory. Am. Nat. 1977, 111, 1169–1194. [Google Scholar] [CrossRef]
  19. Kara, Ö.; Bolat, I.; Çakiroǧlu, K.; Öztürk, M. Plant canopy effects on litter accumulation and soil microbial biomass in two temperate forests. Biol. Fertil. Soils 2008, 45, 193–198. [Google Scholar] [CrossRef]
  20. Tan, X.; Kan, L.; Su, Z.; Liu, X.; Zhang, L. The composition and diversity of soil bacterial and fungal communities along an urban-to-rural gradient in South China. Forests 2019, 10, 797. [Google Scholar] [CrossRef] [Green Version]
  21. Wang, Q.; Wang, W.; He, X.; Zhou, W.; Zhai, C.; Wang, P.; Tang, Z.; Wei, C.; Zhang, B.; Xiao, L.; et al. Urbanization-induced glomalin changes and their associations with land-use configuration, forest characteristics, and soil properties in Changchun, Northeast China. J. Soils Sediments 2019, 19, 2433–2444. [Google Scholar] [CrossRef]
  22. Frouz, J. Effects of Soil Development Time and Litter Quality on Soil Carbon Sequestration: Assessing Soil Carbon Saturation with a Field Transplant Experiment along a Post-mining Chronosequence. Land Degrad. Dev. 2017, 28, 664–672. [Google Scholar] [CrossRef]
  23. Jian, J.; Steele, M.K.; Day, S.D.; Quinn Thomas, R.; Hodges, S.C. Measurement strategies to account for soil respiration temporal heterogeneity across diverse regions. Soil Biol. Biochem. 2018, 125, 167–177. [Google Scholar] [CrossRef]
  24. Hobbie, S.E.; Reich, P.B.; Oleksyn, J.; Ogdahl, M.; Zytkowiak, R.; Hale, C.; Karolewski, P. Tree species effects on decomposition and forest floor dynamics in a common garden. Ecology 2006, 87, 2288–2297. [Google Scholar] [CrossRef]
  25. Dawud, S.M.; Raulund-Rasmussen, K.; Domisch, T.; Finér, L.; Jaroszewicz, B.; Vesterdal, L. Is Tree Species Diversity or Species Identity the More Important Driver of Soil Carbon Stocks, C/N Ratio, and pH? Ecosystems 2016, 19, 645–660. [Google Scholar] [CrossRef] [Green Version]
  26. Liu, X.; Trogisch, S.; He, J.S.; Niklaus, P.A.; Bruelheide, H.; Tang, Z.; Erfmeier, A.; Scherer-Lorenzen, M.; Pietsch, K.A.; Yang, B.; et al. Tree species richness increases ecosystem carbon storage in subtropical forests. Proc. R. Soc. B Biol. Sci. 2018, 285. [Google Scholar] [CrossRef] [Green Version]
  27. Díaz-Pinés, E.; Rubio, A.; Van Miegroet, H.; Montes, F.; Benito, M. Does tree species composition control soil organic carbon pools in Mediterranean mountain forests? For. Ecol. Manag. 2011, 262, 1895–1904. [Google Scholar] [CrossRef]
  28. Vesterdal, L.; Clarke, N.; Sigurdsson, B.D.; Gundersen, P. Do tree species influence soil carbon stocks in temperate and boreal forests? For. Ecol. Manag. 2013, 309, 4–18. [Google Scholar] [CrossRef]
  29. Vesterdal, L.; Schmidt, I.K.; Callesen, I.; Nilsson, L.O.; Gundersen, P. Carbon and nitrogen in forest floor and mineral soil under six common European tree species. For. Ecol. Manag. 2008, 255, 35–48. [Google Scholar] [CrossRef]
  30. Hansen, K.; Vesterdal, L.; Schmidt, I.K.; Gundersen, P.; Sevel, L.; Bastrup-Birk, A.; Pedersen, L.B.; Bille-Hansen, J. Litterfall and nutrient return in five tree species in a common garden experiment. For. Ecol. Manag. 2009, 257, 2133–2144. [Google Scholar] [CrossRef]
  31. Lukina, N.; Kuznetsova, A.; Tikhonova, E.; Smirnov, V.; Danilova, M.; Gornov, A.; Bakhmet, O.; Kryshen, A.; Tebenkova, D.; Shashkov, M.; et al. Linking forest vegetation and soil carbon stock in northwestern Russia. Forests 2020, 11, 979. [Google Scholar] [CrossRef]
  32. Binkley, D.; Giardina, C. Why do tree species affect soils? The Warp and Woof of tree-soil interactions. Biogeochemistry 1998, 42, 89–106. [Google Scholar] [CrossRef]
  33. Polglase, P.J.; Paul, K.I.; Khanna, P.K.; Nyakuengama, J.G.; O’Connell, A.M.; Grove, T.S.; Battaglia, M. Change in Soil Carbon Following Afforestation or Reforestation; Australian Greenhouse Office: Canberra, Australia, 2000; Volume 20. [Google Scholar]
  34. Nakane, K.; Lee, N.J. Simulation of soil carbon cycling and carbon balance following clear-cutting in a mid-temperate forest and contribution to the sink of atmospheric CO2. Vegetatio 1995, 121, 147–156. [Google Scholar] [CrossRef]
  35. Pollierer, M.M.; Langel, R.; Körner, C.; Maraun, M.; Scheu, S. The underestimated importance of belowground carbon input for forest soil animal food webs. Ecol. Lett. 2007, 10, 729–736. [Google Scholar] [CrossRef] [PubMed]
  36. Pardon, P.; Reubens, B.; Reheul, D.; Mertens, J.; De Frenne, P.; Coussement, T.; Janssens, P.; Verheyen, K. Trees increase soil organic carbon and nutrient availability in temperate agroforestry systems. Agric. Ecosyst. Environ. 2017, 247, 98–111. [Google Scholar] [CrossRef]
  37. Cheng, W.; Baoquan, J.; Guangfa, Q.; Jiali, J.; Lin, G.; Chang, Z.; Ruilin, S. Effect and Development Countermeasures of Beijing Plain Afforestation. J. Chin. Urban For. 2017, 15, 6–11. [Google Scholar] [CrossRef]
  38. Li, L. Impacts of Plain Afforestation on Forest Landscape Patterns in Beijing. J. Chin. Urban For. 2020, 18, 5–10. [Google Scholar] [CrossRef]
  39. Wang, M.; Faber, J.H.; Chen, W.; Li, X.; Markert, B. Effects of land use intensity on the natural attenuation capacity of urban soils in Beijing, China. Ecotoxicol. Environ. Saf. 2015, 117, 89–95. [Google Scholar] [CrossRef] [PubMed] [Green Version]
  40. Hui, N.; Liu, X.; Johan Kotze, D.; Jumpponen, A.; Francini, G.; Setälä, H. Ectomycorrhizal fungal communities in urban parks are similar to those in natural forests but shaped by vegetation and park age. Appl. Environ. Microbiol. 2017, 83. [Google Scholar] [CrossRef] [Green Version]
  41. Setälä, H.M.; Francini, G.; Allen, J.A.; Hui, N.; Jumpponen, A.; Kotze, D.J. Vegetation type and age drive changes in soil properties, nitrogen, and carbon sequestration in urban parks under cold climate. Front. Ecol. Evol. 2016, 4, 1–14. [Google Scholar] [CrossRef] [Green Version]
  42. Nero, B.F.; Anning, A.K. Variations in soil characteristics among urban green spaces in Kumasi, Ghana. Environ. Earth Sci. 2018, 77, 1–12. [Google Scholar] [CrossRef]
  43. Thimonier, A.; Sedivy, I.; Schleppi, P. Estimating leaf area index in different types of mature forest stands in Switzerland: A comparison of methods. Forest 2010, 543–562. [Google Scholar] [CrossRef]
  44. Böhm, W. Methods of Studying Root Systems; Springer: Berlin/Heidelberg, Germany, 1979; Volume 21, ISBN 9783642672842. [Google Scholar]
  45. Bauhus, J.; Messier, C. Soil exploitation strategies of fine roots in different tree species of the southern boreal forest of eastern Canada. Can. J. For. Res. 1999, 29, 260–273. [Google Scholar] [CrossRef]
  46. Li, Y.; Bruelheide, H.; Scholten, T.; Schmid, B.; Sun, Z.; Zhang, N.; Bu, W.; Liu, X.; Ma, K. Early positive effects of tree species richness on soil organic carbon accumulation in a large-scale forest biodiversity experiment. J. Plant Ecol. 2019, 12, 882–893. [Google Scholar] [CrossRef]
  47. Zhu, J.; Hu, H.; Tao, S.; Chi, X.; Li, P.; Jiang, L.; Ji, C.; Zhu, J.; Tang, Z.; Pan, Y.; et al. Carbon stocks and changes of dead organic matter in China’s forests. Nat. Commun. 2017, 8, 1–10. [Google Scholar] [CrossRef] [PubMed]
  48. Ghosh, S.; Scharenbroch, B.C.; Ow, L.F. Soil organic carbon distribution in roadside soils of Singapore. Chemosphere 2016, 165, 163–172. [Google Scholar] [CrossRef]
  49. Wold, S.; Sjöström, M.; Eriksson, L. PLS-regression: A basic tool of chemometrics. Chemom. Intell. Lab. Syst. 2001, 58, 109–130. [Google Scholar] [CrossRef]
  50. Błońska, E.; Lasota, J.; Gruba, P. Effect of temperate forest tree species on soil dehydrogenase and urease activities in relation to other properties of soil derived from loess and glaciofluvial sand. Ecol. Res. 2016, 31, 655–664. [Google Scholar] [CrossRef] [Green Version]
  51. Ribbons, R.R.; Kepfer-Rojas, S.; Kosawang, C.; Hansen, O.K.; Ambus, P.; McDonald, M.; Grayston, S.J.; Prescott, C.E.; Vesterdal, L. Context-dependent tree species effects on soil nitrogen transformations and related microbial functional genes. Biogeochemistry 2018, 140, 145–160. [Google Scholar] [CrossRef] [Green Version]
  52. Brumme, R.; Egenolf, M.; Aydin, C.; Block, J.; Meiwes, K.; Wilpert, K. Soil Organic Carbon and Nitrogen in Forest Soils of Germany. In Functioning and Management of European Beech Ecosystems. Ecological Studies; Khanna, P.K., Ed.; Springer: Berlin/Heidelberg, Germany, 2009; Volume 208, ISBN 9789400720596. [Google Scholar]
  53. Bae, J.; Ryu, Y. Land use and land cover changes explain spatial and temporal variations of the soil organic carbon stocks in a constructed urban park. Landsc. Urban Plan. 2015, 136, 57–67. [Google Scholar] [CrossRef]
  54. Guo, L.B.; Halliday, M.J.; Siakimotu, S.J.M.; Gifford, R.M. Fine root production and litter input: Its effects on soil carbon. Plant Soil 2005, 272, 1–10. [Google Scholar] [CrossRef]
  55. Young, I.M. Biophysical interactions at the root-soil interface: A Review. J. Agric. Sci. 1998, 130, 1–8. [Google Scholar] [CrossRef]
  56. Bhattacharya, A.; Saikia, K.; Takhelmayum, M.; Sarkar, P. Carbon sequestration in the bio-edaphic ecosystem of National Highway-27 in Guwahati, Assam, India. Heliyon 2020, 6, e04969. [Google Scholar] [CrossRef] [PubMed]
  57. Toru, T.; Kibret, K. Carbon stock under major land use/land cover types of Hades sub-watershed, eastern Ethiopia. Carbon Balance Manag. 2019, 14, 1–15. [Google Scholar] [CrossRef] [Green Version]
  58. Eni, D.D.; Iwara, A.I.; Offiong, R.A. Analysis of Soil-Vegetation Interrelationships in a South-Southern Secondary Forest of Nigeria. Int. J. For. Res. 2012, 2012, 1–8. [Google Scholar] [CrossRef] [Green Version]
  59. Gholz, H.L.; Vogel, S.A.; Cropper, W.P.; Mckelvey, K.; Ewel, K.C.; Teskey, R.O.; Curran, P.J. Dynamics of canopy structure and light interception in Pinus elliottii stands, north Florida. Ecol. Monogr. 1991, 61, 33–51. [Google Scholar] [CrossRef] [Green Version]
  60. Lal, R.; Stewart, B.A. Urban Soils; Taylor & Francis: Cambridge, UK, 2017; ISBN 978-1-4987-7009-5. [Google Scholar]
  61. Niemelä, J. Urban Ecology: Patterns, Processes, and Applications; Oxford University Press: Oxford, UK, 2011; ISBN 978-0-19-956356-2. [Google Scholar]
  62. Kunstler, G.; Lavergne, S.; Courbaud, B.; Thuiller, W.; Vieilledent, G.; Zimmermann, N.E.; Kattge, J.; Coomes, D.A. Competitive interactions between forest trees are driven by species’ trait hierarchy, not phylogenetic or functional similarity: Implications for forest community assembly. Ecol. Lett. 2012, 15, 831–840. [Google Scholar] [CrossRef] [Green Version]
  63. Cannell, M.G.R. Forest canopies. Endeavour 1995, 19, 133. [Google Scholar] [CrossRef]
  64. Harte, J.; Rawa, A.; Price, V. Effects of manipulated soil microclimate on mesofaunal biomass and diversity. Soil Biol. Biochem. 1996, 28, 313–322. [Google Scholar] [CrossRef]
  65. Bokhorst, S.; Wardle, D.A. Microclimate within litter bags of different mesh size: Implications for the “arthropod effect” on litter decomposition. Soil Biol. Biochem. 2013, 58, 147–152. [Google Scholar] [CrossRef]
  66. Chen, S.; Zou, J.; Hu, Z.; Chen, H.; Lu, Y. Global annual soil respiration in relation to climate, soil properties and vegetation characteristics: Summary of available data. Agric. For. Meteorol. 2014, 198, 335–346. [Google Scholar] [CrossRef]
  67. Rothe, A.; Binkley, D. Nutritional interactions in mixed species forests: A synthesis. Can. J. For. Res. 2001, 31, 1855–1870. [Google Scholar] [CrossRef]
  68. Paul, K.I.; Polglase, P.J.; Nyakuengama, J.G.; Khanna, P.K. Change in soil carbon following afforestation. For. Ecol. Manag. 2002, 168, 241–257. [Google Scholar] [CrossRef]
  69. Huyler, A.; Chappelka, A.H.; Prior, S.A.; Somers, G.L. Influence of aboveground tree biomass, home age, and yard maintenance on soil carbon levels in residential yards. Urban Ecosyst. 2014, 17, 787–805. [Google Scholar] [CrossRef]
  70. Gill, R.A.; Jackson, R.B. Global patterns of root turnover for terrestrial ecosystems. New Phytol. 2000, 147, 13–31. [Google Scholar] [CrossRef]
  71. Vogt, K.A.; Grier, C.C.; Vogt, D.J. Production, Turnover, and Nutrient Dynamics of Above- and Belowground Detritus of World Forests. Adv. Ecol. Res. 1986, 15, 303–377. [Google Scholar] [CrossRef]
  72. Wang, H.; Liu, S.R.; Mo, J.M.; Wang, J.X.; Makeschin, F.; Wolff, M. Soil organic carbon stock and chemical composition in four plantations of indigenous tree species in subtropical China. Ecol. Res. 2010, 25, 1071–1079. [Google Scholar] [CrossRef]
  73. Yates, C.J.; Norton, D.A.; Hobbs, R.J. Grazing effects on plant cover, soil and microclimate in fragmented woodlands in south-western Australia: Implications for restoration. Austral Ecol. 2000, 25, 36–47. [Google Scholar] [CrossRef]
  74. Brubaker, S.C.; Jones, A.J.; Lewis, D.T.; Frank, K. Soil Properties Associated with Landscape Position. Soil Sci. Soc. Am. J. 1993, 57, 235–239. [Google Scholar] [CrossRef]
  75. Cambou, A.; Saby, N.P.A.; Hunault, G.; Nold, F.; Cannavo, P.; Schwartz, C.; Vidal-Beaudet, L. Impact of city historical management on soil organic carbon stocks in Paris (France). J. Soils Sediments 2021, 21, 1038–1052. [Google Scholar] [CrossRef]
  76. Cambou, A.; Shaw, R.K.; Huot, H.; Vidal-Beaudet, L.; Hunault, G.; Cannavo, P.; Nold, F.; Schwartz, C. Estimation of soil organic carbon stocks of two cities, New York City and Paris. Sci. Total Environ. 2018, 644, 452–464. [Google Scholar] [CrossRef] [Green Version]
Forests 12 00394 g001 550
Figure 1. The layout of soil sampling parks (A) and the ring road location (B).
Figure 1. The layout of soil sampling parks (A) and the ring road location (B).
Forests 12 00394 g001
Forests 12 00394 g002 550
Figure 2. Forest traits compared between coniferous and broadleaved forests. Means and standard errors are shown. ** means p < 0.01, *** means p < 0.001, ns means not significant.
Figure 2. Forest traits compared between coniferous and broadleaved forests. Means and standard errors are shown. ** means p < 0.01, *** means p < 0.001, ns means not significant.
Forests 12 00394 g002
Table
Table 1. SOCC (g kg−1) and SOCD (kg m−2) in the coniferous and broadleaved groups in three layers. Results are presented as means ± standard error. Abbreviations: SOCC, soil organic carbon concentration; SOCD, soil organic carbon density. Different letters in the same row of SOCC and SOCD indicate significant differences between layers at the 0.05 level.
Table 1. SOCC (g kg−1) and SOCD (kg m−2) in the coniferous and broadleaved groups in three layers. Results are presented as means ± standard error. Abbreviations: SOCC, soil organic carbon concentration; SOCD, soil organic carbon density. Different letters in the same row of SOCC and SOCD indicate significant differences between layers at the 0.05 level.
LayersTotalConiferous GroupBroadleaved Group
nMean ± SEMean ± SEMean ± SE
SOCC0–10 cm1668.81 ± 0.19 b9.19 ± 0.30 b8.54 ± 0.25 b
10–20 cm1667.62 ± 0.21 a7.95 ± 0.31 a7.40 ± 0.28 a
20–30 cm1627.65 ± 0.21 a8.04 ± 0.28 a7.38 ± 0.29 a
Total (each group)4948.02 ± 0.128.40 ± 0.187.77 ± 0.16
SOCD0–10 cm1661.21 ± 0.031.24 ± 0.041.19 ± 0.03
10–20 cm1661.17 ± 0.031.24 ± 0.051.15 ± 0.04
20–30 cm1621.24 ± 0.031.29 ± 0.041.20 ± 0.04
Total (each group)4941.21 ± 0.021.26 ± 0.031.17 ± 0.03
Table
Table 2. Summary of the best supported partial least squares regression (PLSR) models for forest traits and SOC parameters in different soil layers. RV, response variables; SOCC, soil organic carbon concentration; SOCD, soil organic carbon density; RMSEP, root mean squared error of prediction.
Table 2. Summary of the best supported partial least squares regression (PLSR) models for forest traits and SOC parameters in different soil layers. RV, response variables; SOCC, soil organic carbon concentration; SOCD, soil organic carbon density; RMSEP, root mean squared error of prediction.
RVLayerR2ComponentExplained in RV (%)RMSEP
SOCCTotal0.35342.070.79
0–10 cm0.25239.240.86
10–20 cm0.35245.500.80
20–30 cm0.27238.290.85
SOCDTotal0.29335.830.83
0–10 cm0.18233.700.90
10–20 cm0.36245.830.79
20–30 cm0.21233.020.88
Table
Table 3. The variable importance in projection (VIP) scores of different traits in each model projection. The traits with VIP scores < 1 were culled. Abbreviations: LAI, leaf area index; LIT, semi-decomposed leaf litter; FRB, fine root biomass; H, tree height; UC, under crown height; DBH, diameter at breast height; CA, canopy area; HC, herbaceous vegetation cover; CD, crown density.
Table 3. The variable importance in projection (VIP) scores of different traits in each model projection. The traits with VIP scores < 1 were culled. Abbreviations: LAI, leaf area index; LIT, semi-decomposed leaf litter; FRB, fine root biomass; H, tree height; UC, under crown height; DBH, diameter at breast height; CA, canopy area; HC, herbaceous vegetation cover; CD, crown density.
ModelsLAILITFRBVDHUCDBHCAHCCD
SOCC
Total1.29 1.06 1.611.031.001.23
0–10 cm1.49 1.62 1.33
10–20 cm1.11 1.01 1.24 1.531.02 1.04
20–30 cm1.09 1.07 1.491.21 1.22
SOCD
Total1.12 1.07 1.671.061.131.13
0–10 cm1.25 1.741.05 1.22
10–20 cm1.02 1.01 1.20 1.581.031.09
20–30 cm 1.04 1.461.141.451.08
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Xu, X.; Sun, Z.; Hao, Z.; Bian, Q.; Wei, K.; Wang, C. Effects of Urban Forest Types and Traits on Soil Organic Carbon Stock in Beijing. Forests 2021, 12, 394. https://doi.org/10.3390/f12040394

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Xu X, Sun Z, Hao Z, Bian Q, Wei K, Wang C. Effects of Urban Forest Types and Traits on Soil Organic Carbon Stock in Beijing. Forests. 2021; 12(4):394. https://doi.org/10.3390/f12040394

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Xu, Xinhui, Zhenkai Sun, Zezhou Hao, Qi Bian, Kaiyue Wei, and Cheng Wang. 2021. "Effects of Urban Forest Types and Traits on Soil Organic Carbon Stock in Beijing" Forests 12, no. 4: 394. https://doi.org/10.3390/f12040394

APA Style

Xu, X., Sun, Z., Hao, Z., Bian, Q., Wei, K., & Wang, C. (2021). Effects of Urban Forest Types and Traits on Soil Organic Carbon Stock in Beijing. Forests, 12(4), 394. https://doi.org/10.3390/f12040394

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