Mass loss and nutrient release during the decomposition of sixteen types of plant litter with contrasting quality under three precipitation regimes.

Mass loss and nutrient release during litter decomposition drive biogeochemical cycling in terrestrial ecosystems. However, the relationship between the litter decomposition process and the decomposition stage, precipitation, and litter quality has rarely been addressed, precluding our understanding of how litter decomposition regulates nutrient cycling in various ecosystems and their responses to climate change. In this study, we measured mass loss as well as carbon and nutrient releases during the decomposition of 16 types of leaf litter under three precipitation treatments over 12 months in a common garden experiment (i.e., using standardized soil and climatic conditions). Sixteen types of leaves were divided into three functional groups (evergreen, deciduous, and herbaceous). The objectives were to understand the effects of decomposition stages and precipitation regimes on litter decomposition and to examine the relationship between this effect and chemical properties. The mass loss and release of nitrogen and potassium were significantly higher in the 6- to 12-month stage of decomposition (high temperature and humidity) than in the 0- to 6-month stage. Phosphorus was relatively enriched in evergreen leaves after 6 months of decomposition. The rates of mass loss and nutrient release were significantly greater in herbaceous than in deciduous and evergreen leaves. Increasing precipitation from 400 to 800 mm accelerated mass loss and potassium release but decreased phosphorus release in the 0- to 6-month stage of decomposition. These results highlighted the contribution to and complexity of litter chemical properties in litter decomposition.

INTRODUCTION

The decomposition of litter in ecosystems plays an important role in meclass="Disease">diating major ecosystem class="Chemical">processes (Berg et al., 1993; Salinas et al., 2011; Zhou, Clark, Su, & Xiao, 2015) and sustaining the class="Chemical">productivity and functionality of terrestrial ecosystems (Adair et al., 2008). The breakdown of dead class="Chemical">plant materials and the release of nutrients drive biogeochemical cycles (Cebrian, 1999; Hirobe, Sabang, Bhatta, & Takeda, 2004; Trogisch, He, Hector, & Scherer‐Lorenzen, 2016) and the availability of nutrients to class="Chemical">plants (Swift, Heal, & Anderson, 1979). Litter decomclass="Chemical">position is an integral comclass="Chemical">ponent of the global cycles of class="Chemical">pan class="Chemical">nitrogen (N), phosphorus (P), and carbon (C) and the connection between above‐ and belowground biotic processes (Trogisch et al., 2016). Previous estimations have shown that approximately 90% of global terrestrial plant production is transferred into the dead organic matter pool, and the rest is consumed by herbivores (Cebrian, 1999). Among the production transferred into dead organic matter, approximately 76% is lost to the atmosphere (1.9 Mg C ha−1 year−1) and 24% is redistributed into the soil (Chambers, Schimel, & Nobre, 2001). Therefore, mass loss and nutrient release during the decomposition of litter have important links to ecosystem processes (Berg & McClaugherty, 2013). China's Loess Plateau has semiarid climate conditions (Qiu, Zhang, Cheng, & Yin, 2010). In recent years, vegetation has been restored on the Loess Plateau, and the ecological environment has been improved through a series of measures, such as returning farmland to forests and grasslands and prohibiting logging and grazing. With the development of these projects, the artificial addition of chemical or organic fertilizers has gradually decreased, and plant litter has become the main source of soil organic matter and nutrients in the area. Therefore, the study of the decomposition of plant litter on the Loess Plateau has important theoretical and guiding significance.

Mass loss and nutrient release during decomposition are driven by decomposer interactions with biotic and abiotic factors (Campbell et al., 2016; Cleveland et al., 2014; Lehmann & Kleber, 2015; Tamura, Suseela, Simpson, Powell, & class="Chemical">Tharayil, 2017); most of these factors (e.g., soil moisture and temclass="Chemical">perature, matrix quality, annual evaclass="Chemical">potransclass="Chemical">piration, and soil biological activity) are related to class="Chemical">preciclass="Chemical">pitation and temclass="Chemical">perature (Berg & McClaugherty, 2013; Sanaullah, Rumclass="Chemical">pel, Charrier, & Chabbi, 2012). In most terrestrial ecosystems, soil moisture, which is largely affected by class="Chemical">preciclass="Chemical">pitation, is more imclass="Chemical">portant than temclass="Chemical">perature in influencing litter decomclass="Chemical">position (Gray & Fierer, 2012; Hao, Zhao, Zhao, & Wang, 2010). Stuclass="Chemical">pan class="Disease">dies have shown that variation in microclimate at local scales is an important factor for explaining differences in decomposition rates (Bradford, Berg, Maynard, Wieder, & Wood, 2016; Joly et al., 2017). Nevertheless, water availability could become the dominant factor influencing litter decomposition at local scales, particularly in desert or semiarid regions where water is the primary limiting factor (Couteaux, Bottner, & Berg, 1995; Zhang, Hui, Luo, & Zhou, 2008; Zhang, Zhang, & Gao, 2008). Precipitation has a decisive effect on the spatial distribution of vegetation in most areas of the Loess Plateau and is the main factor influencing the growth and development of vegetation on this plateau. A positive correlation between litter decomposition and precipitation has been observed in tropical rain forests with annual precipitation amounts higher than 5,000 mm (southwestern Costa Rica, Wieder, Cleveland, & Townsend, 2009), arid deserts (the northern Chihuahuan Desert, USA, François, Kurupas, & Throop, 2017), and areas with a midcontinental climate (northeastern Kansas, USA, Reed, Blair, Wall, & Seastedta, 2009). Changes in precipitation can influence litter decomposition by directly restricting the physical breakdown of litter and by indirectly affecting the activity of decomposers (Salamanca, Kaneko, & Katagiri, 2003). In addition, litter decomposition studies conducted in Mediterranean systems found a significant reduction in decomposition with reduced water availability (e.g., Almagro, Maestre, Martĺnez‐LÓpez, Valencia, & Rey, 2015; Santonja, Fernandez, Gauquelin, & Baldy, 2015; Santonja et al., 2017). Previous studies have provided an understanding of how precipitation affects mass loss during decomposition, although the effects on nutrient release have been considered less but are urgently needed given their potential to influence the cycling and availability of nutrients in terrestrial ecosystems (Bloor & Bardgett, 2012; Liu, Liu, Guo, Wang, & Yang, 2014) and the coupled cycling of water and nutrients in most ecosystems, particularly in arid and semiarid climates (Suseela, Tharayil, Xing, & Dukes, 2015).

Litter quality has important regulatory effects on decomposition (Maeda, 2016; Vanholme et al., 2012; Zhou et al., 2015). Among the metrics of litter quality, the contents of N and class="Chemical">lignin and the ratios of class="Chemical">pan class="Chemical">carbon to N (C:N) and lignin:N are considered to be directly related to mass loss and nutrient release during decomposition (Aerts, Van‐Odegom, & Cornelissen, 2012; Berg & McClaugherty, 2011; Li, Han, & Hu, 2008; Melillo, Aber, & Muratore, 1982; Suseela & Tharayil, 2017). For example, Zhang, Hui, et al. (2008), Zhang, Zhang, et al. (2008) found that litter decomposition rates increased with N, P, and K but decreased with C:N, lignin, and lignin:N. Melillo et al. (1982) also showed that litter with high contents of N and P but low C:N ratios decomposed faster than litter with high contents of cellulose, hemicellulose, and lignin. Similar results were reported by Stohlgren (1988a, 1988b). These results, together with many others, indicate that initial concentrations of N, lignin in plant litter, and lignin:N could be good predictors of litter decomposition rates in many ecosystems (Bryant, Holland, Seastedt, & Walker, 1998; Fioretto, Di, Papa, & Fuggi, 2005; Liu, Chen, et al., 2016; Suseela & Tharayil, 2017). Furthermore, the chemical composition of litter during decomposition is affected by precipitation. Hobbie (2000) found that the litter lignin concentration declined with decreasing precipitation in a Hawaiian montane forest. However, to date, whether the regulatory effect of litter quality on mass loss and nutrient release varies with precipitation and decomposition stage has not been examined. There is no quantitative model for the contribution of the chemical properties of litter to mass loss and nutrient release at different stages of decomposition, which hinders the prediction of the effects of litter decomposition on biogeochemical cycles under various global change scenarios.

In this study, we selected leaf litter from 16 plants (four evergreen trees, six deciduous trees, and six herbaceous) to compose a wide range of leaf chemical properties (e.g., N and class="Chemical">lignin contents, and C:N and class="Chemical">pan class="Chemical">lignin:N ratios), allowing us to examine the regulatory effect of leaf chemical properties on mass loss and nutrient release and whether this regulation varies with precipitation and decomposition stage. We present results regarding mass loss and nutrient release during the decomposition of the leaf litter under three precipitation scenarios to test the following hypotheses: (H1) Mass loss and nutrient release will increase with precipitation, and this response will be consistent across three functional groups of leaves; (H2) there will be a stronger mass loss and nutrient release response to different precipitation regimes in the early compared to the late stage of decomposition; and (H3) there is a strong correlation between the chemical properties of litter, and the contribution of these properties to mass loss and nutrient release will follow different models at different stages of decomposition. The objectives were formulated to understand how precipitation and decomposition stage affect mass loss and nutrient release during decomposition and to relate these processes to leaf chemical properties. Such understanding will provide essential information regarding the relationship of litter decomposition parameters and litter traits as well as precipitation, which will be helpful to support the validation and refinement of terrestrial ecological models.

MATERIALS AND METHODS

Study site

This study was carried out in the field experimental site of Northwest A&F University. The site is located in Yangling, Shaanxi, China (34°16′18″N, 108°04′59″E, 525 m a.s.l.), with a mean annual precipitation and temperature of 580.5 mm and 15.6°C, respectively, and it is characterized by a warm‐temperate monsoon climate (Zhang et al., 2012). The monthly mean precipitation and air temperature over a period of 53 years are presented in Figure S1. The soil used in this study was collected from farmland (pH = 7.8) that had been abandoned for at least 8 years. The soil is a Typ‐Eum‐Orthic anthrosol, which belongs to the class="Chemical">Nitisols accorclass="Chemical">pan class="Disease">ding to FAO taxonomy (FAO‐UNESCO, 1988). The concentrations of organic matter, total nitrogen, extractable phosphorus, and potassium were 22.04, 1.63 g/kg, 48, and 490 mg/kg, respectively. The texture of the soil was clay loam, and the gravimetric moisture content at field capacity was 22%. The contents of sand, silt, and clay were 27%, 41%, and 32%, respectively. Given that all the soil used in this study was the same, the effects of the initial soil properties on litter decomposition would be negligible.

Litter material and sampling

To generate a wide span of leaf chemical properties, we selected leaves from 16 species that are widely class="Disease">distributed in Shaanxi Province and vary markedly in their leaf chemical class="Chemical">proclass="Chemical">perties. We selected these sclass="Chemical">pecies accorclass="Chemical">pan class="Disease">ding to the results from our previous investigation so that the leaf chemical properties varied significantly. The 16 species belonged to six deciduous trees, four evergreen trees, and six herbaceous. The deciduous trees were R. pseudoacacia (Robinia pseudoacacia, Leguminosae), P. ningshanica (Populus ningshanica, Salicaceae), M. pumila (Malus pumila, Rosaceae), Q. wutaishanica (Quercus wutaishanica, Fagaceae), B. platyphylla (Betula platyphylla, Betulaceae), and S. psammophila (Salix psammophila, Salicaceae). The evergreen trees were P. orientalis (Platycladus orientalis, Cupressaceae), C. deodara (Cedrus deodara, Pinaceae), P. tabuliformis (Pinus tabuliformis, Pinaceae), and P. serrulata (Photinia serrulata, Rosaceae). The herbaceous species were S. capillata (Stipa capillata, Gramineae), G. max (Glycine max, Leguminosae), O. sativa (Oryza sativa, Gramineae), Z. mays (Zea mays, Gramineae), H. annuus (Helianthus annuus, Compositae), and S. italica (Setaria italica, Gramineae). In August 2014, fresh green leaves were collected before most of the leaves naturally fell and were oven‐dried (40°C) and stored at room temperature. The sampling site and chemical composition of the 16 types of leaves are presented in Table 1.

Table 1

The sampling sites and the mean values of the initial chemical properties of each leaf litter used in this study

	Common name	Latin name	Sampling site	C (g/kg)	N (g/kg)	P (g/kg)	K (g/kg)	C:N	Cellulose (g/kg)	Lignin (g/kg)	Lignin:N
Deciduous	Locust	Robinia pseudoacacia	Fufeng (34°37′N, 107°45′E)	413.3	25.6	1.5	4.3	16.1	294	191	7.5
	Poplar	Populus ningshanica	Yangling (34°16′N, 108°7′E)	411.7	29.0	2.3	9.6	14.2	298	234	8.1
	Apple	Malus pumila	Changwu (35°18′N, 107°38′E)	426.3	24.8	1.7	14.7	17.2	211	132	5.3
	Birch	Betula platyphylla	Fuxian (36°23′N, 108°42′E)	469.6	18.7	2.4	11.5	25.1	443	154	8.2
	Liaodong oak	Quercus wutaishanica	Fuxian (36°23′N, 108°42′E)	438.3	17.8	1.6	7.4	24.6	306	201	11.3
	Salix	Salix psammophila	Shenmu (38°58′N, 110°30′E)	445.1	17.8	1.9	12.4	25.0	237	323	18.2
Evergreen	Pine	Pinus tabuliformis	Yangling (34°16′N, 108°7′E)	488.0	12.4	1.4	5.7	39.5	286	306	24.8
	Cedar	Cedrus deodara	Fufeng (34°37′N, 107°45′E)	447.6	12.6	0.9	4.9	35.5	371	223	17.7
	Arborvitae	Platycladus orientalis	Yangling (34°16′N, 108°7′E)	501.0	10.5	1.1	3.2	47.8	420	205	19.6
	Heather	Photinia serrulata	Yangling (34°16′N, 108°7′E)	430.4	14.1	1.3	8.5	30.5	294	238	16.9
Herbaceous	Sunflower	Helianthus annuus	Hengshan (37°21′N, 110°01′E)	332.1	40.5	3.4	27.5	8.2	191	105	2.6
	Maize	Zea mays	Yangling (34°16′N, 108°7′E)	413.0	26.1	2.9	17.3	15.8	271	185	7.1
	Millet	Setaria italica	Hengshan (37°21′N, 110°01′E)	370.8	20.8	2.1	17.8	17.8	272	173	8.3
	Stipa	Stipa capillata	Guyuan (36º38′N, 106º58′E)	402.4	12.4	1.1	8.6	32.4	319	252	20.3
	Soybean	Glycine max	Hengshan (37°21′N, 110°01′E)	388.7	35.2	2.5	8.1	11.0	250	164	4.7
	Rice	Oryza sativa	Hengshan (37°21′N, 110°01′E)	385.9	27.0	2.6	14.7	14.3	251	152	5.6

C: carbon; N: nitrogen; P: phosphorus; K: potassium.

C: class="Chemical">carbon; N: class="Chemical">pan class="Chemical">nitrogen; P: phosphorus; K: potassium.

As nearly all the leaves fell at the end of the growing season (autumn), our experiment started on 30 November 2014. The litter remaining in each container after 6 and 12 months of decomposition was collected with tweezers and placed in paper bags. For some samples, a very small amount of soil particles was attached to the decomposed litter, and a soft brush was used to remove these attached soil particles very carefully. Therefore, there was very little or no mineral soil attached to the litter, and thus, litter was not analyzed for percentage ash. The litter was oven‐dried at 60°C to a constant weight, weighed to calculate the mass loss during decomposition, and then ground to pass through a 0.25‐mm sieve for chemical analysis.

Experimental setup

In situ litter decomposition experiments were carried out in the field using PVC (class="Chemical">polyvinyl chloride) containers (20 cm in class="Chemical">pan class="Disease">diameter and 20 cm in depth), 10 cm of which was buried in the soil. Six grams of leaf litter was placed into the containers and on the surface of the soil. The samples in the containers were divided into two parts by a separator: One side was designed for the 6‐month decomposition, corresponding to an early stage of decomposition, and the other side was designed for the 12‐month decomposition and was used for calculating the results of late‐stage decomposition by a comparison with the results from the 6‐month decomposition. A nylon net (20 cm in diameter with a 2 mm mesh size) was carefully placed on the litter to minimize the loss of litter by wind and other factors. The details of the experimental design are shown in Figure S3. To minimize the effect of spatial variations in light, temperature, and rainfall, a plastic shed was set up at a 3‐m height above the experimental units. The plastic shed was 11 m long and 6 m wide (Figure S3).

The experimental design included the decomposition stage, precipitation treatments, and litter types. The decomposition stages included 0–6 and 6–12 months of decomposition. Because all 16 plant species used in this study are widely class="Disease">distributed in Shaanxi Province, which is characterized by a class="Chemical">preciclass="Chemical">pitation range of 400–800 mm with a mean class="Chemical">preciclass="Chemical">pitation of 600 mm, the designed class="Chemical">preciclass="Chemical">pitation treatments in this study were 400, 600, and 800 mm class="Chemical">per year, which are caclass="Chemical">pable of caclass="Chemical">pturing the range and average class="Chemical">preciclass="Chemical">pitation regimes. Moreover, the average class="Chemical">preciclass="Chemical">pitation regime used in this study (600 mm) is similar to the 53‐year mean annual class="Chemical">preciclass="Chemical">pitation at the study site (580.5 mm). The class="Chemical">preciclass="Chemical">pitation was controlled by an artificial simulation system (Figure S4), and the rainfall amounts in each treatment during the exclass="Chemical">perimental class="Chemical">periods are class="Chemical">presented in Figure 1. An artificial simulated rainfall system was installed at the toclass="Chemical">p of the shed. The sclass="Chemical">pray range of the class="Chemical">pan class="Chemical">water sprinkler was short, the spray was stable, and a 360° full‐circle spray was applied. The water droplets sprayed from the sprinkler were small enough to simulate raindrops (Figure S4). Each type of leaf litter received a combination of the decomposition stage and precipitation treatments with six replicates, resulting in a total of 288 plots.

Figure 1

The manipulated rainfall in 400, 600, and 800 mm precipitation treatments and air temperature during the experimental period (November 2014–October 2015)

Chemical analysis

The litter before decomposition was prepared for the analysis of the concentrations of C, N, P, K, class="Chemical">lignin, and class="Chemical">pan class="Chemical">cellulose. The samples after 6 and 12 months of decomposition were prepared for the analysis of the C, N, P, and K concentrations. The concentration of C in the litter samples was analyzed using the wet combustion method with potassium dichromate and sulfuric acid oxidation for 5 min followed by titration with 0.2 mol/L FeSO4 (Nelson & Sommers, 1982). A separate sample was wet‐combusted with H2SO4‐H2O2, and a solution was prepared for the measurement of the N, P, and K concentrations (Page, Miller, & Keeney, 1982). The concentration of N in solution was titrated with 0.05 mol/L HCl using an auto Kjeldahl analyzer (FOSS Kjeltec 2300). The concentration of phosphorus in solution was measured by the molybdenum blue colorimetry method. The concentration of potassium in solution was analyzed by the flame emission method (Thermo ICE 3000). The lignin and cellulose concentrations were determined according to the acid detergent lignin method (Vanderbilt, White, Hopkins, & Craig, 2008) with some modifications (He et al., 2016). Briefly, fine litter samples (1.0 g) that were oven‐dried and ground were transferred to digestion tubes and suspended in a solution of H2SO4 (1.0 mol/L) and cetyltrimethylammonium bromide (CTAB; 20 g/L; 80 ml). The tubes were heated at 169°C for 1 hr. After cooling, the tubes were transferred to a sand core funnel (50 ml, G3 specification) and washed with acetone until the solution obtained through the suction filtration was clean. After oven‐drying at 170°C for 1 hr, the sample and tube were weighed together and were designated as W1. Subsequently, the sample was soaked for more than 3 hr in an H2SO4 solution (72%), subjected to suction filtration, and washed with acetone, as described above. The sample was then oven‐dried at 170°C for 1 hr. The sample and tube were then weighed together and were designated as W2, which was placed in a muffle furnace (Box Furnace; Lindberg/Blue M) at 550°C for 3 hr and weighed after cooling (designated as W3). The cellulose concentration was determined from the weight loss difference between W1 and W2 divided by the sample weight (1.0 g) and then multiplied by 100, whereas the lignin concentration was determined as the difference between the W2 and W3 measurements. All analyses were conducted in triplicate.

The pan class="Disease">difference between the initial amounts and those remaining after 6 months was used to calculate total C, N, P, and K release during the 0–6 months of decomclass="Chemical">position. The class="Chemical">pan class="Disease">difference between the amounts remaining after 6 and 12 months was used to calculate total C, N, P, and K release during the 6–12 months of decomposition.

Data analyses

In this study, we defined the early and late stages of decomposition as the 0‐ to 6‐month and 6‐ to 12‐month decomposition, respectively. The rate of mass loss (RM, %) during litter decomposition in each treatment was calculated as follows:where M0 and Mt are the mass (g) of the litter before and after decomposition, respectively, for each stage.

The release rates of C, N, P, and K (RC, class="Chemical">RN, RP, and RK, resclass="Chemical">pectively, %) were calculated as follows: where C0, N0, P0, and K0 are the concentrations (g/kg) of class="Chemical">pan class="Chemical">carbon, nitrogen, phosphorous, and potassium, respectively, in the litter samples before decomposition in each stage, and Ct, Nt, Pt, and Kt are the concentrations of carbon, nitrogen, phosphorus, and potassium, respectively, in the litter samples after decomposition in each stage.

Multiway analysis of variance (ANOVA) was conducted to examine the class="Disease">direct and interactive effects of decomclass="Chemical">position stage (0–6 months vs. 6–12 months), class="Chemical">preciclass="Chemical">pitation (400, 600, and 800 mm), and functional grouclass="Chemical">p of the litter (grass and croclass="Chemical">ps, deciduous, and evergreen) on the rates of mass loss and class="Chemical">pan class="Chemical">carbon and nutrient release (Table 2). In this study, lignin and cellulose were not measured for the samples after 6 and 12 months of decomposition because the amount of residue was not sufficient for the measurement, so the analysis of chemical properties was divided into two decomposition stages. Correlation coefficients among the chemical properties of the respective litter in the 0‐ to 6‐month (Table S2) and 6‐ to 12‐month (Table S3) decomposition stages were also analyzed. Principal component analysis (PCA) was used to identify the relationships between leaf chemical properties of different functional groups (deciduous, evergreen, and herbaceous) in 0‐ to 6‐month and 6‐ to 12‐month stages of decomposition (Figure 4). All the statistical analyses were carried out using SPSS software (version 19.0, IBM). Principal component regression analysis was performed using the R software package v.3.3.2 (R Core Team, 2018).

Table 2

Multiway analysis of variance (ANOVA) for the effects of decomposition stages (ST, 0‐ to 6‐month vs. 6‐ to 12‐month stage), precipitation treatments (PP, 400, 600, and 800 mm per year), and functional groups (FG) on the rates of mass loss and nutrients release

	RM (%)		RC (%)		RN (%)		RP (%)		RK (%)
	F	p	F	P	F	p	F	p	F	p
FG	62.1	<.001	61.1	<.001	123.3	<.001	35.1	<.001	91.4	<.001
PP	2.1	.137	3.1	.047	0.9	.422	1.2	.317	6.6	.001
ST	152.9	<.001	245.5	<.001	103.6	<.001	509.8	<.001	561.3	<.001
FG × PP	0.8	.525	0.5	.754	1.3	.262	0.4	.821	0.4	.797
FG × ST	2.1	.130	4.5	.012	5.5	.004	3.7	.025	22.6	<.001
ST × PP	1.5	.229	2.8	.065	1.5	.217	16.9	<.001	12.0	<.001
ST × FG×PP	0.2	.916	0.4	.829	0.6	.694	0.1	.983	1.1	.343
RMSE	1.308		1.306		1.439		1.609		1.108
R 2	.348		.440		.422		.540		.585
p	<.001		<.001		<.001		<.001		<.001
F	10.567		6.460		9.734		4.179		3.010

RM: mass loss rate; RC: carbon release rate; RN: nitrogen release rate; RP: phosphorous release rate; RK: potassium release rate; RMSE: root mean square error.

Figure 4

Principal component analysis used to identify the relationships between leaf chemical properties of different functional groups (deciduous, evergreen, and herbaceous) in 0‐ to 6‐month (a) and 6‐ to 12‐month (b) stages of decomposition. Loadings included are displayed as C, N, P, K, C:N, N:P, C:P, cellulose, lignin, cellulose:N, lignin:N, cellulose:P, and lignin:P. C: carbon; N: nitrogen; P: phosphorus; and K: potassium. Principal components 1 and 2 (shown) best described the relationship between leaf chemical properties

RM: mass loss rate; RC: class="Chemical">carbon release rate; class="Chemical">pan class="Chemical">RN: nitrogen release rate; RP: phosphorous release rate; RK: potassium release rate; RMSE: root mean square error.

RESULTS

Mass loss and carbon release during decomposition

As expected, the rate of mass loss (RM) was significantly higher in the 6‐ to 12‐month stage of decomposition (46.69 ± 1.5%, mean ± SE) than that in the 0‐ to 6‐month stage of decomposition (27.25 ± 0.8%) when averaged across the 16 leaf types and three precipitation treatments (p < .001, Figure 2a). Furthermore, the effects of precipitation on the RM varied with the decomposition stage (Figure 3b). The average RM across the 16 species was significantly higher in the 600 and 800 mm treatments (28.29 ± 1.4 and 29.94 ± 1.5%, respectively) than in the 400 mm treatment (23.43 ± 1.3%) (p < .05) in the 0‐ to 6‐month stage but was not affected by the precipitation treatments in the 6‐ to 12‐month stage (46.79 ± 2.3, 45.72 ± 2.6, and 47.60 ± 2.8% for the 400, 600, and 800 mm treatments, respectively).

Figure 2

(a) The mass loss rate (RM, %) and release rates of carbon (RC, %), nitrogen (RN, %), phosphorous (RP, %), and potassium (RK, %) in 0‐ to 6‐month and 6‐ to 12‐month stages of decomposition. Different lowercase letters indicate significant difference between 0‐ to 6‐month and 6‐ to 12‐month stages of decomposition. (b) The mass loss rate (RM, %) and release rates of carbon (RC, %), nitrogen (RN, %), phosphorous (RP, %), and potassium (RK, %) in different functional groups. Different lowercase letters indicate significant difference in different functional groups. (c) The mass loss rate (RM, %) and release rates of carbon (RC, %), nitrogen (RN, %), phosphorous (RP, %), and potassium (RK, %) in different precipitation treatments. Different lowercase letters indicate significant difference in different precipitations. Error bars denote two standard errors of the mean

Figure 3

(a) The mass loss rate (RM, %) and release rates of carbon (RC, %), nitrogen (RN, %), phosphorus (RP, %), and potassium (RK, %) in 0‐ to 6‐month and 6‐ to 12‐month stages of decomposition in different functional groups. Different lowercase letters indicate significant difference among functional groups in same decomposition stage. (b) The mass loss rate (RM, %) and release rates of carbon (RC, %), nitrogen (RN, %), phosphorous (RP, %), and potassium (RK, %) in 0‐ to 6‐month and 6‐ to 12‐month stages of decomposition under 400, 600, and 800 mm precipitation treatments. Different lowercase letters indicate significant difference among precipitation treatments in same decomposition stage. Error bars denote two standard errors of the mean

(a) The mass loss rate (RM, %) and release rates of class="Chemical">carbon (RC, %), class="Chemical">pan class="Chemical">nitrogen (RN, %), phosphorous (RP, %), and potassium (RK, %) in 0‐ to 6‐month and 6‐ to 12‐month stages of decomposition. Different lowercase letters indicate significant difference between 0‐ to 6‐month and 6‐ to 12‐month stages of decomposition. (b) The mass loss rate (RM, %) and release rates of carbon (RC, %), nitrogen (RN, %), phosphorous (RP, %), and potassium (RK, %) in different functional groups. Different lowercase letters indicate significant difference in different functional groups. (c) The mass loss rate (RM, %) and release rates of carbon (RC, %), nitrogen (RN, %), phosphorous (RP, %), and potassium (RK, %) in different precipitation treatments. Different lowercase letters indicate significant difference in different precipitations. Error bars denote two standard errors of the mean

(a) The mass loss rate (RM, %) and release rates of class="Chemical">carbon (RC, %), class="Chemical">pan class="Chemical">nitrogen (RN, %), phosphorus (RP, %), and potassium (RK, %) in 0‐ to 6‐month and 6‐ to 12‐month stages of decomposition in different functional groups. Different lowercase letters indicate significant difference among functional groups in same decomposition stage. (b) The mass loss rate (RM, %) and release rates of carbon (RC, %), nitrogen (RN, %), phosphorous (RP, %), and potassium (RK, %) in 0‐ to 6‐month and 6‐ to 12‐month stages of decomposition under 400, 600, and 800 mm precipitation treatments. Different lowercase letters indicate significant difference among precipitation treatments in same decomposition stage. Error bars denote two standard errors of the mean

The RM was significantly higher in the litter from the herbaceous (46.59 ± 1.5%) but was significantly lower in the litter from the evergreen trees (25.68 ± 1.4%) compared with the litter from the deciduous trees (35.22 ± 1.6%) (p < .001) when averaged across the two decomposition stages and precipitation treatments (Figure 2b). Although there was great variation in the RM among the litter from the 16 species (Table [Link], [Link]), the effects of the functional group were consistent across the decomposition stage, with a significantly higher RM for the herbaceous but a lower RM for the evergreen trees within each of the combinations (Figure 3a). Therefore, the functional groups dominated the mass loss during the decomposition of the leaf litter regardless of the decomposition stage and precipitation treatments in this study.

The release rate of pan class="Chemical">carbon (RC) during litter decomclass="Chemical">position was significantly and class="Chemical">positively correlated with the RM (Figure S2) and therefore showed a similar resclass="Chemical">ponse class="Chemical">patteclass="Chemical">pan class="Chemical">rn to the decomposition stage, precipitation treatment, and functional groups in this study (Table 2).

Nutrient release during decomposition

The release rate of N during decomposition (class="Chemical">RN) was 108% higher in the 6‐ to 12‐month stage than in the 0‐ to 6‐month stage of decomclass="Chemical">position (class="Chemical">p < .001) and varied with the functional grouclass="Chemical">ps of the leaves (class="Chemical">p < .001) (Figures 2a and 3a) The class="Chemical">pan class="Chemical">RN was significantly higher in the leaf litter from the herbaceous (53.94 ± 1.3%) but lower in the leaf litter from the evergreen trees (21.50 ± 1.8%) compared with the litter from the deciduous trees (34.84 ± 1.8%) when averaged across the two stages and three precipitation treatments (p < .001, Figure 2b). The RN in the 6‐ to 12‐month stage of decomposition was 37, 156, and 191% higher than in the 0‐ to 6‐month stage for the herbaceous, evergreen, and deciduous trees, respectively, when averaged across the three precipitation treatments (Figure 3a).

The class="Chemical">RN was not affected by the class="Chemical">preciclass="Chemical">pitation treatment in the 0‐ to 6‐month and 6‐ to 12‐month stages of decomclass="Chemical">position (Figure 3b). When tested within each functional grouclass="Chemical">p, no significant class="Chemical">pan class="Disease">differences in RN in response to precipitation were observed. Therefore, the RN was less dependent on precipitation than on the functional group and stage of decomposition in this study.

The release rates of P and K during decomposition (RP and RK) were significantly affected by the functional group of the leaves and the stage of decomposition (Table 2). When averaged across the two stages of decomposition, the RP and RK were significantly higher for the herbaceous (35.94 ± 2.2 and 75.94 ± 1.1%) than for the evergreen trees (16.94 ± 2.3 and 56.86 ± 2.1%) and deciduous trees (32.86 ± 2.1 and 66.59 ± 1.4%) (Figure 2b). When averaged across the three functional groups of leaves, the RP and RK were 460 and 78% higher, respectively, in the 6‐ to 12‐month stage than in the 0‐ to 6‐month stage of decomposition (p < .001) (Figure 3a).

In this study, the RP and RK were not affected by the precipitation treatment when averaged across the two stages of decomposition (Figure 2c). In the 0‐ to 6‐month stage of decomposition, the RP was significantly higher in the 400 mm precipitation treatment (14.71 ± 2.0%) but lower in the 600 mm (7.31 ± 1.9%) and 800 mm (3.05 ± 3.0%) precipitation treatments. In the 6‐ to 12‐month stage of decomposition, the RP was significantly higher in the 800 mm precipitation treatment (p < .05), which was the opposite of the 0‐ to 6‐month stage of decomposition (Figure 3b). The RK increased significantly with precipitation (p < .001) in the 0‐ to 6‐month stage of decomposition but was not altered by precipitation (p > .05) in the 6‐ to 12‐month stage of decomposition (Figure 3b).

The dependence of mass loss and nutrient release on litter chemical properties

There are many leaf chemical properties that affect mass loss and nutrient release. To investigate the correlation between these chemical properties, we performed a whole correlation analysis in the 0‐ to 6‐month (Table S2) and 6‐ to 12‐month (Table S3) stages of decomposition. The results inclass="Disease">dicate that in this study, there was a significant correlation between all leaf chemistry class="Chemical">proclass="Chemical">perties (exceclass="Chemical">pt for some N:P ratios). Princiclass="Chemical">pal comclass="Chemical">ponent analysis (PCA) was used to identify the relationshiclass="Chemical">ps between leaf chemical class="Chemical">proclass="Chemical">perties of class="Chemical">pan class="Disease">different functional groups (deciduous, evergreen, and herbaceous) in the 0‐ to 6‐month and 6‐ to 12‐month stages of decomposition. Principal components 1 and 2 (shown) best described the relationship between leaf chemical properties: 0–6 and 6–12 months explained 85.7% and 78.8%, respectively (Figure 4). We found that each functional group was evenly distributed in the graph, and different precipitation regimes were also evenly distributed in the graph (not shown). We also found a significant correlation among chemical properties, and the distribution of the chemical properties in the graph did not change much between 0–6 months and 6–12 months (Figure 4). These results indicated that as the decomposition time increased, the same release trend occurred among the compounds.

Principal component analysis used to identify the relationships between leaf chemical properties of class="Disease">different functional grouclass="Chemical">ps (deciduous, evergreen, and herbaceous) in 0‐ to 6‐month (a) and 6‐ to 12‐month (b) stages of decomclass="Chemical">position. Loaclass="Chemical">pan class="Disease">dings included are displayed as C, N, P, K, C:N, N:P, C:P, cellulose, lignin, cellulose:N, lignin:N, cellulose:P, and lignin:P. C: carbon; N: nitrogen; P: phosphorus; and K: potassium. Principal components 1 and 2 (shown) best described the relationship between leaf chemical properties

When looking at the mean value of the three functional groups in Figure 4, we found that N, P, and K can be used as representative chemical properties of herbaceous; N:P can be used as a representative chemical property of deciduous trees; and C, C:N, C:P, and class="Disease">difficult‐to‐decomclass="Chemical">pose substances and their stoichiometric ratios (e.g., class="Chemical">pan class="Chemical">cellulose, lignin, cellulose:N, cellulose:P, lignin:N, and lignin:P) can be used as representative chemical properties of evergreen trees. It is interesting that the later stage of decomposition had basically the same response pattern as the early stage of decomposition. Although we did not measure cellulose and lignin in the 6‐ to 12‐month stage, according to the distribution of the characteristics in the figure and the correlation among the characteristics (Tables S2 and S3), we concluded that lignin and cellulose are the representative properties of evergreen trees. Therefore, the chemical properties of the litter itself did not change during decomposition.

DISCUSSION

Our results showed that mass loss and C and K release were significantly greater in the higher precipitation treatment than in the lower precipitation treatment at the early decomposition stage but were minimally affected by precipitation at the late stage of decomposition. Furthermore, the mass loss and nutrient release were regulated by the litter chemical properties, and the contribution of these chemical properties would have class="Disease">different models at class="Chemical">pan class="Disease">different stages of decomposition. These results partially support our hypotheses and indicate that the time of decomposition and climate together mediate litter decomposition and nutrient cycling.

In our study, the mass loss rate was higher in the 6‐ to 12‐month (46.69%) than in the 0‐ to 6‐month (27.25%) decomposition stage. This trend was not in agreement with the exponential function of mass loss, where the mass rate decreases with time of decomposition (Corrigan & Oelbermann, 2010; Wu, Li, & Wan, 2013). Previous stuclass="Disease">dies have shown that class="Chemical">pan class="Species">Creosote bush (Larrea tridentata) fine litter mass loss over a 3‐month period accounted for approximately 20% of the original mass (Moorhead & Reynolds, 1989), and litter mass loss after 21 days of incubation in the laboratory was extremely low (<3%) (Gomes, Ferreira, Tonin, Adriana, & José, 2017). The results from Gomes, Medeiros, and Gonçalves (2016) showed 17.5% mass loss for Maprounea guianensis litter after 10 days of incubation in laboratory microcosms. Additionally, leaching loss of mass dominated the decomposition in the early stage (Berg & McClaugherty, 2013), while the accumulation of lignin and cellulose and other refractory substances inhibited decomposition at the late stage (Voříšková & Baldrian, 2013). Regarding long‐term decomposition, it has been shown that mass loss in a Mediterranean shrubland in southern France varied between 18.6% (Ulex) and 36.5% (Cistus) after 1 year and between 27.0% (Ulex) and 53.0% (Quercus) after 2 years (Santonja et al., 2019). However, it should be noted that our study covered only the early stage of decomposition according to the definition used, and the average temperature (5.2°C) and precipitation (11.8 mm) of the 0‐ to 6‐month stage of decomposition were significantly lower than the average temperature (22.5°C) and precipitation (21.1 mm) of the 6‐ to 12‐month stage of decomposition (Figure 1). A low‐temperature and low‐humidity environment will reduce decomposition (Liu, Chen, et al., 2016; Sardans, Rivas‐Ubach, & Penuelas, 2012; Wang, Li, & Bai, 2000); thus, the decomposition rate in the 0‐ to 6‐month stage was less than that in the 6‐ to 12‐month stage. Therefore, the effects of litter decomposition remain uncertain, mainly due to differences in experimental setups (mass loss classes vs. specific time span) and ecosystem types (forests vs. shrubland).

Our results showed that the RM followed the order of herbaceous > deciduous leaves > evergreen leaves, which is in agreement with previous observations (Coclass="Chemical">rnwell et al., 2008; Gholz, Weclass="Chemical">pan class="Disease">din, Smitherman, Harmon, & Parton, 2000; Wu et al., 2013). For example, Cornwell et al. (2008) found that the decomposition of litter from deciduous species was 60% faster than that from evergreen litter. Similarly, Wu et al. (2013) reported that in a 2‐year in situ decomposition experiment, the mass loss after 336 and 701 days was greater for deciduous leaves (ca. 30% and 40%, respectively) than for evergreen leaves (ca. 15% and 25%, respectively) in Chinese temperate forests. The higher RM of the herbaceous and deciduous leaves than that of the evergreen leaves was mainly due to the lower contents of lignin and cellulose and lower C:N and C:lignin ratios (Wu et al., 2013, Table 1). Gomes et al. (2016) found 17.5% mass loss for M. guianensis litter after 10 days of incubation in laboratory microcosms. Moretti, Gonçalves, Ligeiro, and Callisto (2007), Alvim, Medeiros, Rezende, and Gonçalves (2015), and Medeiros et al. (2015) found 5%–15% leaf mass loss for several Cerrado plant species (herbaceous) after 1 week of field incubation and a maximum 20% mass loss after 30 days. Hättenschwiler and Jørgensen (2010) found that at a forest experimental site (consisting of approximately 140 evergreen species) near Sinnamary, French Guiana, after approximately 7 months of field treatment, the average remaining litter mass changed between 25.2% and 71.3%, which is higher than our study for the mass loss during the early stage of decomposition. In this study, we found that the RM and litter C were significantly negatively correlated (Figure S5), which can also explain the changes in the RM between various functional groups of leaves.

We showed that the release rates of nutrients were greater in the 6‐ to 12‐month stage than in the 0‐ to 6‐month stage of decomposition, which was consistent with the effects of stage on the RM and RC (Figure 2a). These results suggest that the release of nutrients is coupled with mass loss during leaf decomposition. We observed a relative enrichment of P (negative RP) in the evergreen leaves at the 0‐ to 6‐month stage of decomposition, probably because the mass loss was faster than the P release and leaching from the litter. An alteclass="Chemical">rnative exclass="Chemical">planation is the immobilization of P in microbial biomass at the early stage of decomclass="Chemical">position because most decomclass="Chemical">position is P‐limited (Liu, Liu, et al., 2016; Liu, Chen, et al., 2016). In this study, among the 16 leaf tyclass="Chemical">pes, the N, P, and K contents of the evergreen sclass="Chemical">pecies were significantly lower than those of the deciduous and herbaceous sclass="Chemical">pecies, while the C, C:N, class="Chemical">pan class="Chemical">cellulose, lignin, and lignin:N were significantly higher (Table 1). Therefore, the decomposition of these leaves was limited by the availability of P, while the acquisition of P by microorganisms in soils may result in the relative enrichment of P in litter. This explanation is supported by observations that the P concentration increased gradually during the decomposition of Malus domestica leaf litter and was positively correlated with mass loss (Han et al., 2011). In this study, when averaged across all the leaves, the rate of P release in the 6‐ to 12‐month stage (50.74 ± 1.6%) was almost six times the rate in the 0‐ to 6‐month stage of decomposition (8.80 ± 1.4%), probably because P is mainly distributed in refractory substances and combines with lignin and cellulose, which decompose during the late stage of decomposition (Suzuki, Makino, & Mae, 2001).

Our results further showed that significantly higher nutrient release occurred from the herbaceous and deciduous leaves than from the evergreen leaves (p < .001, Figure 2b), which is consistent with the patteclass="Chemical">rns of influence of functional grouclass="Chemical">ps on the RM (Figure 2b). These results were class="Chemical">primarily due to variations in leaf quality and thus decomclass="Chemical">position class="Chemical">processes, as class="Chemical">pan class="Disease">discussed above. This explanation was supported by previous observations in an alpine forest–tundra ecotone on the eastern Tibetan Plateau, where the nutrient loss from deciduous leaves (ca. 60%) was twice that from evergreen leaves (ca. 30%) after 360 days of decomposition (Liu, Chen, et al., 2016). Pérezsuárez, Arredondomoreno, Hubersannwald, and Vargashernández (2009) also found that after 4 and 7 months of decomposition, N loss from deciduous leaves (ca. 11% and 55%) was higher than that from evergreen leaves (ca.‐25% and 50%) in central‐northwest Mexico. Our results therefore provide further evidence that nutrient cycling is faster and that the soil nutrient content is higher in deciduous forests than in evergreen forests (Arunachalam & Singh, 2002; Nsabimana, Haynes, & Wallis, 2004).

The effects of precipitation on mass loss and nutrients during decomposition

We demonstrated that the effects of precipitation on mass loss varied with decomposition stage, with an accelerated RM during the 0‐ to 6‐month stage due to increased precipitation but an unchanged RM during the 6‐ to 12‐month stage. This is probably because the decomposition of class="Chemical">water‐soluble substances and class="Chemical">pan class="Chemical">carbohydrates (decomposition mainly in the early stage) is sensitive to precipitation, while the decomposition of lignin, cellulose, and refractory substances (decomposition mainly in the late stage) is relatively stable with precipitation (Wang et al., 2017). Austin and Vitousek (2000) showed that the mass loss of all common litter increases with increasing precipitation in Hawaii, USA. Our results are in agreement with previous observations in tropical (Wieder et al., 2009), temperate (Reed et al., 2009; Song et al., 2009), and arid and semiarid (François et al., 2017; Hao et al., 2010) climates and are in line with the theory that the effects of rainwater on the mass loss of leaf litter are due to the leaching of labile compounds (Halima, Biyanzi, & Ibrahima, 2008; Lockaby, Wheat, & Clawson, 1996; Salamanca et al., 2003). Therefore, changes in the labile fraction of litter during decomposition merit consideration in investigating litter mass loss under various climate conditions.

Our results showed that the class="Chemical">RN was not affected by class="Chemical">preciclass="Chemical">pitation, suggesting the stable release of litter N with class="Chemical">preciclass="Chemical">pitation. This observation contrasts with class="Chemical">previous finclass="Chemical">pan class="Disease">dings that precipitation and thus soil moisture drive N cycling during the decomposition of various types of leaf litter (Burke, Lauenroth, & Parton, 1997) and that the interactions of soil water and N availability regulate litter decomposition (Zhang, Hui, et al., 2008; Zhang, Zhang, et al., 2008). Austin and Vitousek (2000) showed that the initial litter mass in Hawaii, USA, changed significantly with the amount of precipitation, ranging from 500 to 5,500 mm mean annual precipitation, after 2 years of decomposition, and the nitrogen content increased with the increase in precipitation. Similarly, Santonja et al. (2019) indicated that experimental reduction in precipitation will have a negative effect on C and N release after 2 years rather than after 1 year of decomposition. Therefore, the lack of a response of the RN to precipitation in this study might be due to the relatively narrow precipitation regimes (400–800 mm) and shorter decomposition time.

Our results showed that the RP and RK were mostly affected by precipitation in the 0‐ to 6‐month stage of decomposition (Figure 3b). The decreased RP in the 0‐ to 6‐month stage of decomposition in response to precipitation might be due to the limiting effect of P on decomposition. As class="Disease">discussed earlier, P may be transclass="Chemical">ported from soil to litter by microorganisms during the early stage of decomclass="Chemical">position, and this class="Chemical">process will result in the relative enrichment of P in some litter can and be accelerated by increased class="Chemical">preciclass="Chemical">pitation. Austin and Vitousek (2000) also class="Chemical">pointed out that immobilization of litter occurred at all locations in a wetland for uclass="Chemical">p to 6 months, and the P loss will be reduced. However, in our study, during the 6‐ to 12‐month stage of decomclass="Chemical">position, RP increased significantly with increasing class="Chemical">preciclass="Chemical">pitation, inclass="Chemical">pan class="Disease">dicating that phosphorus fixation only occurred in the first half of the year. The increased RK in the 0‐ to 6‐month stage with precipitation might be ascribed to enhanced decomposition with higher precipitation compared to the lower precipitation treatment. This response pattern was similar to that of mass loss (thus C release), probably because K mainly exists in the cytosol, chloroplasts, and glycophytic tissues (Petra, 2012), which decompose. In this study, C release was significantly positively correlated with K release (Figure S2). Our results of the effects of precipitation on K release are consistent with previous results, which showed that up to 33% of K from leaf litter is lost due to leaching (Gessner & Schwoerbel, 1989) because K is highly mobile and not structurally bound (Mahmood et al., 2009).

Changes in precipitation have inclass="Disease">direct effects on mass loss and nutrient release and leaching during litter decomclass="Chemical">position by influencing soil moisture (Adair et al., 2008; Suseela, class="Chemical">pan class="Chemical">Tharayil, Xing, & Jeffrey, 2013). High precipitation results in high soil moisture and thus high activities of soil microbes and litter decomposition (Allison et al., 2013). In this study, we used a uniform decomposition medium, so it is considered that when the precipitation increases, the soil moisture content will be increased, so the soil moisture during the 12‐month decomposition was not measured. We recommend that soil moisture measurements be included in future research.

The measurement of the initial chemical metrics (C, N, P, and K, and class="Chemical">cellulose and class="Chemical">pan class="Chemical">lignin contents) enabled us to examine the relationships of these factors with the mass loss and nutrient release during the 0‐ to 6‐month and 6‐ to 12‐month decomposition stages. We demonstrated that leaf chemical properties have important regulations on mass loss and nutrient release during decomposition, which is consistent with previous findings in various ecosystems and litter (Austin & Vitousek, 2000; Ding et al., 2012; Gibson, 2012). The previously reported variation was due to carbohydrate decomposition at the early stage and lignin and cellulose and other refractory substance decomposition at the late stage (Corrigan & Oelbermann, 2010; Lambers, Chapin‐Iii, & Pons, 2008), indicating that the early mass loss was greater than the late mass loss. However, in this study, most litter decomposition mainly occurred at the late stage, mainly due to the higher temperature in this stage than in the early stage, which provides an explanation for the similar determination of leaf mass loss and the release of most nutrients. Studies have also shown that an increase in the N content after 2 months of decomposition in an Alaskan boreal forest accelerated total mass loss and cellulose loss (Talbot & Treseder, 2012). The decomposition of lignin and cellulose and other refractory substances is more dependent on the availability of N than on that of carbohydrates (Lambers et al., 2008; Song et al., 2009; Zhang, Hui, et al., 2008; Zhang, Zhang, et al., 2008). For example, Hobbie (2000) found that the N supply enhanced the mass loss of litter and the decomposition of lignin in a Hawaiian montane forest. Similar to this conclusion, in this study the N content of herbaceous was significantly higher than that of deciduous and evergreen trees, so the mass loss of herbaceous was significantly higher than that of other functional groups. Generally, the rates of mass loss and nutrient release during decomposition decreased with higher initial C, cellulose, and C:N, C:P, N:P, and lignin:N ratios in the leaf litter, and there was no fixed pattern of the effects of N, P, and K. Therefore, lower C, cellulose, and lignin enhanced mass loss and the corresponding nutrient release during decomposition (Gautam, Lee, Song, Lee, & Bong, 2016; Song, Zhou, Gu, & Qi, 2015; Vestgarden, 2001).

Although the mass loss of the three functional groups increased during the 6‐ to 12‐month stage of decomposition, the mass loss of the herbaceous was still significantly higher than that of deciduous and evergreen trees. We found that as the decomposition time increased, the same release trend was observed among the functional group compounds, so the RM, RC, class="Chemical">RN, RP, and RK were basically the same in the 0‐ to 6‐month and 6‐ to 12‐month stages of decomclass="Chemical">position. Therefore, we found that within the range of small class="Chemical">preciclass="Chemical">pitation graclass="Chemical">pan class="Disease">dients, the mass loss and nutrient release of leaf litter in each functional group did differ greatly and were determined by the chemical characteristics of the litter itself. We speculate that the same conclusion will be obtained over a range of large precipitation gradients and longer decomposition times, and of course, we look forward to further demonstration by researchers in the future.

CONCLUSION

In this study, a common garden experiment was conducted to measure mass loss and class="Chemical">carbon and nutrient release during the decomclass="Chemical">position of 16 tyclass="Chemical">pes of leaf litter in three class="Chemical">preciclass="Chemical">pitation treatments. The mass loss and nutrient release were greater in the 6‐ to 12‐month stage than in the 0‐ to 6‐month stage of decomclass="Chemical">position and were greater for the herbaceous and deciduous leaves than for the evergreen leaves. class="Chemical">pan class="Chemical">Phosphorus was relatively enriched in the evergreen leaves at the early stage of decomposition (0–6 months). Increased precipitation (from 400 to 800 mm) accelerated mass loss and potassium release but decreased phosphorus release at the early stage of decomposition. However, precipitation had less effect on mass loss and nutrient release at the 6‐ to 12‐month stage of decomposition. Furthermore, the results indicate that in this study, there was a significant correlation between all leaf chemistry properties (except for some N:P ratios), and mass loss and nutrient release were significantly correlated with leaf chemical metrics. Within the small range of the precipitation regime, with the extension of the decomposition time, the relationship between the chemical properties of the litter, the mass loss, and nutrient release of leaf litter for each functional group did not differ greatly, and all were determined by their own chemical properties.

In this study, we investigated the mass loss and nutrient release during litter decomposition with respect to decomposition stages and precipitation regimes under controlled conclass="Disease">ditions. Under field conclass="Chemical">pan class="Disease">ditions, litter contains fractions of contrasting initial compositions due to the mixture of multiple species and plant parts. Furthermore, litter contains a mix of residual compositions due to multiple cohorts and a mix of litter decomposition stages. Therefore, the mixing effects of various species and various decomposition stages should be further studied to obtain a general pattern closer to field conditions.

CONFLICT OF INTEREST

None declared.

AUTHOR CONTRIBUTIONS

Qiu LP, Wei XR, and Du NN planned and designed the research. Du NN and Zhang YJ performed experiments and conducted fieldwork. Du NN analyzed the data. All authors pan class="Disease">discussed the results and wrote the manuscriclass="Chemical">pt.

FigS1

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FigS2

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FigS3

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FigS4

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FigS5

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TableS1A

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TableS1b

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TableS2

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TableS3

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FigS1‐S5_caption

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