ABSTRACT It is essential to understand how the loss of biodiversity impacts both ecosystem function (EF) and multifunctionality (EMF). Previous studies have mostly focused on predicting how

species richness (SR) impacts EMF, while the effect of functional diversity (FD) on EMF remains unclear. Specifically, we know little about the primary functional drivers impacting EMF

compared with SR. Therefore, we analysed 8 ecosystem functions within 58 natural secondary forest plots to investigate the effect of FD on both individual EF and EMF. Our results suggest

that SR and FD had very significant positive effects on plant phosphorus, soil available phosphorus, and soil total nitrogen. FD explained significantly more variations in these functional

regression model and random forest analysis, we found that SR and FD were both drivers of EMF but that FD had a stronger effect and could explain more variation. As such, we conclude that FD

drives ecosystem multifunctionality more than SR. SIMILAR CONTENT BEING VIEWED BY OTHERS PLANT DIVERSITY ENHANCES ECOSYSTEM MULTIFUNCTIONALITY VIA MULTITROPHIC DIVERSITY Article 29 August

2024 RELATIONSHIPS BETWEEN SPECIES RICHNESS AND ECOSYSTEM SERVICES IN AMAZONIAN FORESTS STRONGLY INFLUENCED BY BIOGEOGRAPHICAL STRATA AND FOREST TYPES Article Open access 08 April 2022

RESOURCE AVAILABILITY ENHANCES POSITIVE TREE FUNCTIONAL DIVERSITY EFFECTS ON CARBON AND NITROGEN ACCRUAL IN NATURAL FORESTS Article Open access 04 October 2024 INTRODUCTION Biodiversity is

crucial for sustaining ecosystem processes and functioning1. Biodiversity is declining at an unprecedented rate and will continue to decline over the 21st century2. As such, understanding

how the loss of biodiversity impacts ecosystem functioning has become an important goal in biology and conservation3. The study of the relationship between biodiversity and ecosystem

functioning (hereafter, BEF) has been ongoing for over twenty years4,5. Many empirical studies have demonstrated that a loss of biodiversity can lead to reductions in ecosystem functioning6

and the ecosystem services that provide a multitude of benefits to humans7,8. Progress in studies focused on BEF has been spurred with the deepening of understanding, and scientists found

that ecosystems can perform multiple functions or services simultaneously1,9. Thus, multifunctionality (hereafter, EMF) has been generally accepted in recent years and is defined as “the

simultaneous provision of multiple functions”10. Because different species have different functional traits, they could contribute different ecosystem functions. Thus, biodiversity might

have an important effect on the multifunctionality11. Most experiments conducted on the relationship between biodiversity and ecosystem multifunctionality (hereafter, BEMF) have focused on

species richness (hereafter, SR) as the primary metric of biodiversity1,9,10,11,12,13,14 because SR is defined as the number of species and is easily measured. However, some studies suggest

that functional diversity (hereafter, FD) is a stronger predictor of ecosystem functioning15,16,17. The effect is most immediate mainly because the effect of FD is the result of interactions

between species and their environment relative to the species traits15. The reason for FD as a stronger predictor may be due to high FD causing an increase in the utilization efficiency of

environmental resources, which can subsequently promote ecosystem productivity and strengthen defences against diseases, insect pests, and disturbances18,19. Developing a better

understanding of the links between diversity and ecosystem functioning is especially important in forest ecosystems. Forests provide innumerable benefits for humans, including timber,

nutrient and water cycling, and recreational opportunities, among many others8,13. Despite this, previous studies on BEMF have mostly focused on experimental grassland

ecosystems1,20,21,22,23. Regarding forests, more attention has been paid to temperate and boreal forests. Most of studies proved that higher biodiversity was necessary to maintain multiple

ecosystem functions among different ecosystems, but little attention has been paid to subtropical forests8,24,25,26. We noticed that some scientists, such as Mouillot _et al_.27,

Valencia-Gómez _et al_.28 and Finney & Kaye29, conducted many studies on the influence of FD on EMF. These studies found that FD could increase multifunctionality. However, this result

was found in grasslands, dry lands or agricultural systems, and we did not identify related studies on forests to date. Here, we seek to help fill this gap using data collected from a _Pinus

yunnanensis_ forest in southwest China30. We used data collected from 58 natural secondary forest plots located in Qiubei and Shuangbai County in Yunnan Province, China (Fig. 1) and

examined eight individual ecosystem functions (plant nitrogen, plant phosphorus, soil hydrolysable nitrogen, soil available phosphorus, soil total nitrogen, soil total phosphorus, soil total

carbon, and woody plant biomass). Aboveground biomass was the primary key function in the BEMF study8,31. In the soil samples, soil total carbon, soil total nitrogen, soil hydrolysable

nitrogen, soil total phosphorus and soil available phosphorus represent good substitutions related to carbon (C), nitrogen (N) and phosphorus (P) cycling9,21. Nitrogen and phosphorus are two

important nutrient elements for plants. Nitrogen mainly determined photosynthetic C fixation and plant productivity32. Phosphorus is considered necessary for the storage and reproduction of

genetic information and is mainly involved in energy-related processes of living organisms33. Regardless of whether nitrogen or phosphorus was limited, plant growth was affected. Plant

nitrogen and plant phosphorus are considered nutrient pools in aboveground biomass21. We used this unique dataset to address two primary questions: (1) How do SR and FD influence individual

ecosystem functions?; (2) Does FD predict EMF better than SR? We expected to identify the relative importance of biotic and abiotic variables on EMF in a _Pinus yunnanensis_ natural

secondary forest. RESULTS EFFECT OF BIODIVERSITY ON INDIVIDUAL ECOSYSTEM FUNCTIONS Regarding individual functions, the relationships between SR and plant phosphorus (PP) (_r_ = 0.442, _p_ 

< 0.01), soil available phosphorus (SAP) (_r_ = 0.331, _p_ < 0.05) and soil total nitrogen (STN) (_r_ = 0.261, _p_ < 0.05) were all significantly positive. SR accounted for 19.7%,

12.3% and 8% of the variation in these variables, respectively (Table 1). The results were similar when analysing FRic. FRic had a significantly positive correlation with PP (_r_ = 0.500,

_p_ < 0.01), SAP (_r_ = 0.451, _p_ < 0.01) and STN (_r_ = 0.310, _p_ < 0.05), although the total amount of explained variation was higher than SR in all cases (Table 1). For plant

nitrogen (PN), soil hydrolysable nitrogen (SHN), soil total phosphorus (STP), soil total carbon (STC) and woody plant biomass (WPB), there were no significant correlations with SR and FRic

(Table 1). BEMF RELATIONSHIPS BASED ON THE AVERAGING APPROACH Both SR and FRic were related to EMF. SR explained 16.11% of the variation in EMF, while FRic explained 20.72% of the variation.

SR was significantly positively correlated with FRic (_R_2 = 0.7847, _P_ < 0.001) (Fig. 2). EFFECT OF SR AND FRIC ON EMF SR had a positive effect on EMF at thresholds between 12%

(minimum threshold, _T_min) and 91% (maximum threshold, _T_max) (Fig. 3a), and FRic had a positive effect on EMF at thresholds between 8% (minimum threshold, _T_min) and 97% (Fig. 3b). The

relationship between SR and EMF peaked at a threshold of 55% (threshold of maximum diversity effect, _T_mde), where each additional species was associated with 0.22 functions provided at

levels above the threshold (realized maximum effect of diversity, _R_mde) (Fig. 3a). The relationship between FRic and EMF also peaked at a threshold of 55%, but each increase in FRic was

associated with 0.31 functions (Fig. 3b). The maximum possible effect of SR (percentage of maximum possible diversity effect, _P_mde) for our experiment was 36.75%, and the _P_mde of FRic

was 41.85% (Fig. 3). ESTIMATION OF THE RELATIVE CONTRIBUTION OF THE BIOTIC AND ABIOTIC FACTORS TO EMF The results of the multivariate linear regression model suggested FRic of the biotic

factor had a significant positive effect on EMF. The absolute value of the standardized regression coefficients of FRic (0.6535) was the biggest among these variables, indicating that FRic

had the strongest impact on EMF compared with other factors. SR of the biotic factor and the abiotic factors, including soil pH, MAP and MAT, had no significant effect on EMF (Table 2).

According to random forest analysis, we found that FRic had the highest importance for EMF in all variables. In contrast, SR had the lowest importance among all selected variables. For the

abiotic factors, the rank of importance was MAP, MAT, and soil pH (Fig. 4). THE STANDARDIZED EFFECT SIZE (SES) VALUE OF FRIC AND EIGHT INDIVIDUAL EFS The above results demonstrated that FRic

was the main driver for EMF. For individual EFs, the SES values of FRic and PN, PP, SHN, SAP, STN, STP, and SOC were positive. The order of SES value was PP (3.8224) > SAP (3.4224) >

STN (2.3323) > SHN (1.9707) > STC (1.8746) > STP (1.7986) > PN (0.0997). The SES value of FRic and WPB was minimal and negative; the value was −0.0846 (Table 3). DISCUSSION The

primary goal of this work was to determine the relationship between biodiversity and multiple measures of ecosystem function. We found that both SR and FRic were positively correlated with

three of the eight potential components of ecosystem functioning: plant phosphorous, soil available phosphorus and soil total nitrogen. Furthermore, these effects were observed when

combining different measures and calculating ecosystem multifunctionality. Importantly, in all cases, we found that FRic was a better predictor than SR. Functional diversity is thought to be

declining worldwide34. The number of studies about the relationships between functional diversity and ecosystem functioning is increasing. However, the role of functional diversity in EMF

has not been fully explored. This notion is particularly true for forest communities, which have been less well studied within the context of BEMF. In this study, we found that several

individual ecosystem functions, such as plant phosphorus, soil available phosphorus and soil total nitrogen, were sensitive to changes in SR and FRic. For the two metrics of biodiversity, SR

and FRic, the relationship between them and the individual ecosystem functions was relatively consistent. However, FRic could explain more variations in these three ecosystem functions than

SR. These results were consistent with most previous studies17,35,36. It is worth mentioning that SR and FRic had no effect on woody plant biomass in this study, and the result was not

consistent with previous conclusions of BEF studies37. This difference could be due to the structure of the _Pinus yunnanensis_ natural secondary forest. In this forest type, _Pinus

yunnanensis_ held an absolutely dominant position relative to other species30. _Pinus yunnanensis_ contributed 91.73% of the biomass in our study, so increasing or decreasing one species

might not have a significant effect on the biomass. When considering multiple ecosystem functions simultaneously, biodiversity likely has a stronger effect22. In our study, this conclusion

was confirmed regardless of whether SR or FRic served as the metric of biodiversity. Our results also indicate no strong trade-offs between different functions in the _Pinus yunnanensis_

natural secondary forest (Table S2). Normally, trade-offs between different functions are commonplace within local communities1,20,38. However, at larger spatial scales, heterogeneity in a

community composition causes different parts of the landscape to provide different ecosystem functions under the precondition that different species provide different ecosystem

functions1,13,20. In theory, this implies that all ecosystem functions could be maximized simultaneously if information on their causal relationships is known. These results were consistent

with the results of van der Plas _et al_.26, who found that trade-offs were weak among different functions at larger scales. We used the multiple threshold approach to evaluate whether and

when SR or FRic were important drivers of EMF. We obtained a complete picture of how SR or FRic drove EMF by combining some metrics; FRic had an obvious positive effect on EMF at thresholds

between 8% (minimum threshold) and 97% (maximum threshold). This range was wider than that for SR. Byrnes _et al_.10 indicated that if the _T_min was low, the _T_max was high, and both the

_T_mde and the _R_mde remained high, diversity would have a strong effect on EMF. Compared with that observed for SR, these parameters all had the strongest effect at a moderate threshold

(_T_mde = 55%). However, _R_mde and _P_mde values of FRic were greater than those of SR; therefore, our results at least showed that the effect of FRic on EMF was greater than that of SR. In

the multivariate linear regression model and random forest analysis, we all found that FRic was the main driver in BEMF. Our result is consistent with previous studies27,28,29. Compared

with taxonomic diversity for grassland, dry land, agricultural or subtropical forest ecosystems, functional diversity is the strongest predictor of EMF and has a positive effect. For EFs, in

our study, functional diversity has a positive effect with the expectation of WPB (Table 3) because functional diversity is based on functional traits. Functional traits are the key

mechanism by which single species and groups of species affect ecosystem functions39. It should be noted that there is an inevitable connection between SR and FRic40. In this study, we

observed a strong correlation between these variables (_P_ < 0.001, _R_2 = 0.7847). Because FRic is influenced by SR, it is somewhat difficult to tease apart the fraction of variation

that is uniquely explained by functional diversity41. This problem could potentially be resolved using experimental studies in combination with variance partitioning analyses. CONCLUSIONS We

found that 3 of 8 ecosystem functions, PP, SAP and STN, were strongly correlated with SR and FRic. However, FRic could explain more variations in these three ecosystem functions. Using a

multiple threshold approach, we proved that the effect of FRic on EMF was greater than the effect of SR. In addition, we found no strong trade-offs among ecosystem functions in the _Pinus

yunnanensis_ natural secondary forest. Thus, all ecosystem functions may be maximized simultaneously. Moreover, our findings provide strong evidence that FRic drives EMF more than SR. For

ecosystem managers, our findings are useful. Functional diversity was based on multiple functional traits. Thus, to increase EMF, the managers could start with species assemblages and chose

species with functional traits as different as possible. To conserve biodiversity, we reinforce the view that if conserving or promoting biodiversity is the target in an ecosystem, ensuring

a moderate level of EMF is at least a precondition25. MATERIALS AND METHODS PLOT SELECTION AND SAMPLING Field surveys were conducted in April 2015. In total, 58 forest plots measuring 20 × 

20 m were established under the most representative vegetation over an extensive area (approximately 9, 000 km2). Across all plots, the mean annual temperature ranged from 15.7 to 18.2 °C,

the mean annual precipitation ranged from 954 to 1202 mm, and the altitude ranged from 1065 to 2125 m. For our study, the number of plots was sufficient to statistically detect the

relationship between biodiversity and ecosystem functioning42. We selected plots with a gradient of plant species to detect the relationship between biodiversity and ecosystem functions and

tried to minimize other confounding factors, for example, selected the forest of the same age, undisturbed soil and plant community structure. Within the plots, we collected information on

species identity, height, DBH, and spatial location for all individuals >1 cm DBH. For each forest plot, we obtained the MAT and MAP data from ClimateAP (University of British Columbia,

Vancouver, British Columbia, Canada) developed by Wang _et al_.43. For all species, we also collected 50–100 sun-exposed mature leaves from the middle or upper part of the trees from five to

ten individuals. All samples were carefully placed into paper bags and marked. We then measured leaf morphological characteristics using a laser area metre (LI-COR 3100C Area Meter, LI-COR,

USA). The leaf area of _Pinus yunnanensis_ was estimated as a cylinder, so we measured the diameter (_d_) and the length (_L_) by a Vernier calliper (precision: 0.02 mm). The leaf area of

_Pinus yunnanensis_ was calculated with the following formula: LA = 2π\(\sqrt{3}\)/9·_dL_44. All leaf samples were dried for 72 h at 60 °C, and the dry weight for each leaf was measured

immediately with an electronic balance (precision: 0.0001 g). Afterwards, all samples were ground to a fine powder using a ball mill (NM200, Retsch, Haan, Germany) to measure plant N and P

content. We also obtained 5–10 branches (1 cm ≤ DBH ≤ 2 cm) from some shrub species (DBH ≤ 5 cm). We used the water replacement method to measure branch volume after removing the peel. Then,

all branches were dried for 72 h at 103 °C and subsequently weighed. The density of the branches was calculated as the ratio of the dry weight to the volume. For trees and shrubs >5 cm

DBH, we sampled the wooden core by the growth cone. The volume was measured using the diameter and the length of the wooden core, and the wood density was calculated as the ratio of the dry

weight to the volume of the wooden core. All functional traits were measured following standardized protocols45. For each plot, we collected 5 soil samples (0–20 cm) and mixed them evenly.

The soil samples were sieved by a 2-mm mesh and air-dried for one month prior to physiochemical analyses. DEFINING BIODIVERSITY We used species richness (SR) and functional richness (FRic)

as our measures of biodiversity. To correspond to species richness, FRic was used to measure functional diversity. We chose three commonly used plant functional traits to calculate

functional diversity, including leaf area (LA, mm2), specific leaf area (SLA = leaf area/dry weight, mm2·mg−1), and wood density (WD = wood dry weight/wood volume, g·cm−3). These traits were

expected to be related to the acquisition and utilization of resources in plants, including trees46. MEASUREMENT OF INDIVIDUAL ECOSYSTEM FUNCTIONS We measured eight ecosystem properties or

characteristics (used as proxies of functions) linked to total nutrient pools, nutrient cycling, and biological productivity. These ecosystem functions were as follows: plant nitrogen, plant

phosphorus, soil hydrolysable nitrogen, soil available phosphorus, soil total nitrogen, soil total phosphorus, soil total carbon, and woody plant biomass. These ecosystem functions were

consistent with previous studies21,47. Soil total carbon, plant nitrogen and soil total nitrogen were measured by combustion in a CHN elemental analyser (2400II CHN elemental analyser,

PerkinElmer, Boston, MA, USA). Soil available phosphorus was measured by the Olsen method. Soil total phosphorus and plant phosphorus were measured by molybdenum antimony blue colourimetry.

Soil hydrolysable nitrogen was measured by alkaline hydrolysis diffusion. Based on the DBH and height of every individual plant, we estimated the biomass of the 54 investigated species of

woody plants by the growth equation (Table S1). If some species had no growth equation, we chose the growth equation of a similar species instead48. For less frequently occurring species, we

chose the growth equation proposed by Ali _et al_.49 to estimate the biomass following the suggestion of Lambert _et al_.50. Prior to calculating the metrics of multifunctionality, we first

analysed the correlations between the eight functional variables to determine whether they were strongly correlated with one another (Table S2). Among the 28 pairs of relationships, 12

pairs showed significant relationships. However, one exception was noted in that the relationship between soil total carbon and plant nitrogen was slightly negative (_r_ = −0.282, _p_ < 

0.05). Therefore, this finding suggested the lack of no strong trade-offs among the different functions51. ASSESSING EMF We used two complementary approaches to evaluate the role of SR and

FRic in driving EMF. The first was the averaging approach9. To obtain an averaged multifunctionality index for each site, we first calculated the standardized _Z_ scores for the eight

variables. The _Z_ scores were then averaged to obtain a multifunctionality index9. We next used the multiple threshold approach10. Here, we tallied the number of measured functions that

simultaneously exceeded multiple critical thresholds, and the threshold was defined as a given percentage of the highest performance for each function. To eliminate potential outliers, the

highest performing was defined as an average of the top five values for each function52. For our analysis, we selected threshold values ranging from 1 to 99%. For these two approaches, the

averaging approach has been widely used in analyses of multifunctionality12,28,53, and the index has good statistical properties. Specifically, it allows us to directly estimate the ability

of a community to sustain multiple functions simultaneously9,21. It is more suitable for linear model analysis10. To date, in the reported approaches, the multiple threshold approach is the

most comprehensive method to evaluate BEMF relationships10,25. This approach can provide more powerful information and flexibility than other approaches10. STATISTICAL ANALYSES We first

evaluated the relationships between biodiversity (i.e., SR and FRic) and individual ecosystem functions using Pearson correlation and OLS regression analysis. The relationships among SR,

FRic and EMF were evaluated using simple OLS regressions. We then used the multiple threshold method to evaluate the effect of SR and FRic on EMF. _T_min is the minimum threshold where SR or

FRic begins to have an effect. _T_max is the threshold beyond which the slope first declined and was not significantly different from zero. _T_mde is the threshold where SR or FRic had its

strongest effect. _R_mde is the realized maximum effect of SR and FRic, which is the strength of the linear relationships of SR or FRic-multifunctionality where SR or FRic has the strongest

effects. _P_mde is the percentage of the maximum possible SR or FRic effect10. According to these parameters, the effect of SR on EMF could be compared with the effect of FRic on EMF38. We

conducted a multivariate linear regression model to evaluate the comprehensive effects of biotic factors (FRic, SR) and abiotic factors (Soil pH, MAP and MAT) on EMF in the _Pinus

yunnanensis_ natural secondary forest. To select the best model, we employed different alternative models, such as abiotic factors entered first or species richness entered first into the

multivariate linear regression model (Table S3). Then, we used random forest analysis to tease apart the relative importance of these variables on ecosystem multifunctionality. Random forest

analysis was used widely because it could determine the effect of each predictor variable individually and could also interact with other predictors in a multivariable manner54. Lastly, we

used “_impact_” software55 to calculate standardized effect size (SES) of functional diversity obtained using null models that control for SR effect and eight individual EFs. SES value = 

(valuesobserved − mean(valuesnull))/sd (valuesnull). If the SES value was positive, it would indicate divergence from random. In contrast, if the SES value was negative, it would indicate a

random clustering pattern. All statistical analyses were conducted using R version 3.3.256 (R development Core Team, 2016). FRic was calculated in the ‘FD’ package57, and the multiple

threshold analysis was performed in the ‘multifunc’ package10. The standardized regression coefficients were calculated by package ‘QuantPsyc’ in R. The partial regression coefficients were

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1.0–12 (2014). Download references ACKNOWLEDGEMENTS This research was funded by the Fundamental Research Funds of CAF (CAFYBB2017ZX002) and the National Natural Science Foundation of China

(31660236). We would also like to thank Dr. Murphy Stephen at Yale University for his assistance with the English language and grammatical editing of the manuscript. AUTHOR INFORMATION

AUTHORS AND AFFILIATIONS * Research Institute of Resources Insects, Chinese Academy of Forestry, Kunming, 650224, China Xiaobo Huang, Jianrong Su, Shuaifeng Li, Wande Liu & Xuedong Lang

* Pu’er Forest Ecosystem Research Station, National Forestry and Grassland Administration, Kunming, 650224, China Xiaobo Huang, Jianrong Su, Shuaifeng Li, Wande Liu & Xuedong Lang

Authors * Xiaobo Huang View author publications You can also search for this author inPubMed Google Scholar * Jianrong Su View author publications You can also search for this author

inPubMed Google Scholar * Shuaifeng Li View author publications You can also search for this author inPubMed Google Scholar * Wande Liu View author publications You can also search for this

author inPubMed Google Scholar * Xuedong Lang View author publications You can also search for this author inPubMed Google Scholar CONTRIBUTIONS Xiaobo Huang conducted the field measurements

and drafted the manuscript. Jianrong Su conceived the study and revised the manuscript. Shuaifeng Li, Wande Liu and Xuedong Lang conducted the field measurements. CORRESPONDING AUTHOR

Correspondence to Jianrong Su. ETHICS DECLARATIONS COMPETING INTERESTS No conflict of interest exists in the submission of this manuscript, and the manuscript has been approved by all

authors for publication. I would like to declare on behalf of my co-authors that the work described is original research that has not been published previously and is not under consideration

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diversity drives ecosystem multifunctionality in a Pinus yunnanensis natural secondary forest” RIGHTS AND PERMISSIONS OPEN ACCESS This article is licensed under a Creative Commons

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http://creativecommons.org/licenses/by/4.0/. Reprints and permissions ABOUT THIS ARTICLE CITE THIS ARTICLE Huang, X., Su, J., Li, S. _et al._ Functional diversity drives ecosystem

multifunctionality in a _Pinus yunnanensis_ natural secondary forest. _Sci Rep_ 9, 6979 (2019). https://doi.org/10.1038/s41598-019-43475-1 Download citation * Received: 25 June 2018 *

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