Retracted: Distributions of trace elements with long‐term grazing exclusion in a semi‐arid grassland of inner Mongolia

Abstract

We still know little about the distributions of trace elements in grassland with long‐term grazing exclusion. The contents, stocks, and proportions of iron (Fe), aluminum (Al), manganese (Mn), and boron (B) in green plant–litter–root–soil were evaluated by enclosing for 18‐, and 39 years inside the fence (F18 and F39) and grazing outside the fence (F0) in Mongolia grassland. Results showed that F18 and F39 decreased the stocks of Fe, Al, and Mn in green plant and root compared with F0 (p < .05), while increased the stocks of them in litter (p < .05). The F18 obviously increased the stocks of Fe and Mn in soil, especially B (p < .05). The stock of Fe, Al, and Mn in green plant at F39 was 28.6%, 13.9%, and 39.2% higher than that at F18. The stocks of trace elements in undecomposed litter at F39 were increased by 12.7%–52.2% compared with F18, while the stocks of them in complete decomposed litter were decreased by 32.2%–42.5%. The stocks of trace elements in soil at F39 were 9.1%–28.0% lower than that at F18, especially B (p < .05). In conclusion, the trace elements were mainly shifted from green plant and root to soil and complete decomposed litter with 18‐year grazing exclusion. The trace elements were shifted from complete decomposed litter and soil to root with 39‐year grazing exclusion compared with 18‐year grazing exclusion.

INTRODUCTION

Inner Mongolia grassland is one of the most important temperate grasslands, and the livestock husbandry is the preponderant industry in this region. However, 70% of grassland has been degraded because of the factors of nature and human (Bai et al., 2015; Deng et al., 2014; Hafner et al., 2012; Lin et al., 2015; Piñeiro et al., 2009; Wang et al., 2017; Yan et al., 2009). The function of the grassland ecosystem is significantly reduced (Liu et al., 2019; Mcsherry & Ritchie, 2013; Steffens et al., 2008). Grassland degradation seriously affects the yield and quality of pasture (Zhou et al., 2011), and hence threatens the livestock husbandry (Kang et al., 2007).

In recent decades, grazing exclusion has been widely regarded as an effective management strategy for restoring degraded grassland around the world (Golodets et al., 2010; Hu et al., 2016; Javier et al., 2016; Shrestha & Stahl, 2008; Wu et al., 2010). Many studies on grazing exclusion have shown that it has impacts on the diversity and biomass of vegetation (Deng et al., 2014; Golodets et al., 2010; Pei et al., 2008; Wu et al., 2009), soil physical structures and chemical properties, and mineral nutrients in plant or soil (Congio et al., 2021; Hu et al., 2020). However, variations in region, climate, pasture type, and grazing exclusion time have resulted in inconsistent results (He, 2019). Studies have found that long-term grazing exclusion can promote the restoration of vegetation and soil in degraded grasslands (Liu et al., 2017; Wang et al., 2018). However, long-term grazing exclusion has resulted in excessive accumulation of litter on the surface of soil (Hou et al., 2019; Wang et al., 2017). This has a variety of effects on community structure and ecosystem function, and even causes the secondary retrograde succession (Cheng et al., 2016; Ren et al., 2016). The 32-year grazing exclusion reduced the biodiversity and productivity of vegetation (Zhao et al., 2018). The 38-year grazing exclusion in the semi-arid grasslands of Inner Mongolia reduced most of nutrients in the surface soil (Hu et al., 2020). Therefore, the reasonable duration of long-term grazing exclusion is critical to restore degraded grasslands.

Litter is the vegetation that cannot conduct photosynthesis. Its quantity is related to the biomass of green plants (Hou et al., 2019; Wang et al., 2017). The decomposition of litter is of great significance to the nutrient return from plant to soil in grassland (Ball et al., 2014; Wang et al., 2011). It is mainly depended on the soil properties and plant characteristics (Naeem et al., 2021; Song et al., 2017). In addition, the high soil moisture induced by large litter cover can improve the nutrient availability of soil (Deutsch et al., 2010). The root biomass of grasslands is 2–30 times higher than the above-ground standing biomass (Chen et al., 2006; Naeem et al., 2021; Scurlock & Olson, 2002). The variations of productivity and composition of above-ground community and soil physical–chemical properties in grassland are vital for the allocations of photosynthetic products between above-ground and below-ground (Gao et al., 2008). In sum, green plant, litter, root, and soil in grassland should be viewed as an entirety to deeply understand the nutrient cycle of grassland. However, there is less information for the interrelationship of the green plant–litter–root–soil system in the grassland.

Trace elements are the essential mineral nutrients in the grassland ecosystem (Hansch & Mendel, 2009; Yadav, 2010), their contents only accounted for 1% of the dry matter of pasture. The lack or excess of trace elements is an important factor that restricts the yield and quality of pasture and the health of animal. This causes enormous economic losses to the herders (Shen et al., 2006; Xin et al., 2011). Grazing exclusion can alter the trace elements in soil, such as increasing iron (Fe) and manganese (Mn) and decreasing aluminum (Al; Oliveira Filho et al., 2019), thereby changing the content of these elements in pasture (Han et al., 2011; Liu et al., 2014). The different resorption efficiencies of trace elements play crucial roles in the allocation of trace elements in green plant and litter (Millett et al., 2010). The research on the cycle of trace elements can help us maintain the community structure and ecosystem function of grassland, as well as better understand the deficiency and toxicity of trace elements in pasture. This can help us find the limiting factors of livestock (Ågren, 2008). Unfortunately, we do not know much about the distributions of trace elements in green plant–litter–root–soil in grasslands, especially in grasslands with long-term grazing exclusion.

The objectives of this study are as follows: (1) exploring the distributions of Fe, Al, Mn, and B in green plant–litter–root–soil in grassland with 18- and 39-year grazing exclusion and (2) revealing the sensitivity and response of trace elements to long-term grazing exclusion. We hypothesize that proportions of trace elements in green plant–litter–root–soil would be altered with different years of long-term grazing exclusion. This study will provide a scientific basis for the restoration of degraded grasslands, and the study of trace elements in semi-arid grasslands of Inner Mongolia.

METHODOLOGY Study site and experimental design

This study was conducted at the Inner Mongolia Grassland Ecosystem Research Station (IMGERS, 43°38′N, 116°42′E) of the Chinese Academy of Sciences, which is located in Xilin River Basin of Inner Mongolia, China. The region has a semi-arid grassland climate with the annual average temperature of 2.3°C. The annual average precipitation is 330 mm. The annual evaporation is 4~5 times of the precipitation. The soil is described as a dark chestnut, with a loamy sand texture (Bai et al., 2015). The original forage species were Stipa grandis and Leymus chinensis, and the mean percentage of S. grandis and L. chinensis was 57% and 21%, respectively. Strong winds occur from March to May, and the average monthly speed can reach 4.9 m/s. Wind erosion and dust storms are the common phenomena in this region. These contribute to the matter balance (Hoffmann et al., 2008).

The experimental site is composed of three plots, including the 39-year grazing plot outside of fence (F0), the 18-year grazing exclusion plot inside of fence (F18, grazing exclusion from 2001) and 39-year grazing exclusion plot inside of fence (F39, grazing exclusion from 1980; Figure 1). The grazing intensity was 5 sheep/hm²/year in the long-term grazing plot. The information of density, species and biomass of plant in these three plots were listed in Table 1.

FIGURE 1. Grazing plot (a), enclosing 18 years plot (b), and enclosing 39 years plot (c).

TABLE 1 The basic information of F0, F18, and F39 plots.

	F0	F18	F39
Species (number/m2)	9.40 ± 1.35b	8.90 ± 2.13b	14.50 ± 2.72a
Density (plant/m2)	454.60 ± 33.41a	148.70 ± 15.27b	118.90 ± 6.23b
Green plant biomass (g/m2)	88.62 ± 4.55b	131.40 ± 8.88a	128.77 ± 5.96a
L1 biomass (g/m2)	25.42 ± 1.44b	185.90 ± 31.79a	229.09 ± 76.50a
L2 biomass (g/m2)		182.80 ± 11.74a	136.94 ± 9.94b
L3 biomass (g/m2)		360.30 ± 105.15a	246.23 ± 61.12b
0–20 cm root biomass (g/m2)	15.89 ± 0.50a	13.63 ± 0.15b	14.42 ± 0.36b
20–50 cm root biomass (g/m2)	9.31 ± 0.09a	8.82 ± 0.11b	9.15 ± 0.15a
50–100 cm root biomass (g/m2)	8.90 ± 0.09a	8.74 ± 0.08a	8.98 ± 0.10a

Note: L1, undecomposed litter; L2, incomplete decomposed litter; L3, complete decomposed litter. Lowercase letter in row indicates significant difference at 0.05 level among treatments (ANOVA).

Sampling and analysis

A typical transect (100 m long) was randomly located in each plot in August 2019. Ten quadrats were established at 10 m intervals in each transect for vegetation and soil sampling. Plant, litter, root, and soil samples were collected in the same quadrat of 1 m × 1 m. Plant and litter were weighed after dried in 105°C in the laboratory. Litter was divided into undecomposed litter, incomplete decomposed litter, and complete decomposed litter according to the decomposition state of the litter. Three soil cores were collected (0–10, 10–20, 20–30, 30–50, 50–70, and 70–100 cm depth) from each soil sampling location to make a composite sample. Soil samples were placed into plastic bags and then air-dried in the laboratory. Then, the soils were sieved through a 2-mm sieve and used for determination. The root samples were collected using the method of soil auger. One soil core was collected (0–10, 10–20, 20–30, 30–50, 50–70, 70–100 cm depth) from each soil sampling location. The 0–10 and 10–20 cm samples were mixed as 0–20 cm root sample, and 20–30 and 30–50 cm samples were mixed as 20–50 cm root sample, and 50–70 and 70–100 cm samples were mixed as 70–100 cm root sample. The root samples were packed into mesh bag and were washed by deionized water. Then root were collected after dried in 105°C.

The Fe, Al, Mn, and B contents in plant and soil were determined using a flame atomic absorption machine (Varian Model AA240).

Statistical analysis

All data were statistically analyzed using a 10.0 SPSS software. We calculated the standard errors and compared the means of parameters among different treatments through one-way analysis of variance (ANOVA). The least significant difference test was performed. Pearson correlation was used to assess the relationships of trace element contents among green plant, litter, root, and soil.

The equation of stock of mineral element is as follows:

Mineral element stock in soil (g/m²) = mineral element content (g/kg) × bulk density (g/cm³) × soil deep (cm) × 10,000. Mineral element stock in plant (green plant, litter, and root) (g/m²) = mineral element content (g/kg) × dry matter of plant (g/m²) × 10⁻³.

The equation of the mineral element reuse efficiency is as follows:

Mineral element reuse efficiency (%) = (mineral element content in green plant − mineral element content in litter)/mineral element content in green plant × 100% (Feller et al., 2002; Killingbeck, 1996).

RESULTS Contents

The content of Fe, Al, Mn, and B in green plant at F18 was 86.2%, 79.5%, 63.0%, and 41.2% lower than that at F39, respectively (p < .05). F39 greatly increased the B content in green plant compared with F18 (p < .05; Table 2).

TABLE 2 The contents of trace elements in grassland system after long-term grazing exclusion (Mean ± SE).

	Fe (g/kg)			Al (g/kg)			Mn (mg/kg)			B (mg/kg)
	F0	F18	F39	F0	F18	F39	F0	F18	F39	F0	F18	F39
Green plant	1.30 ± 0.3a	0.18 ± 0.0b	0.20 ± 0.0b	1.22 ± 0.3a	0.25 ± 0.1b	0.21 ± 0.0b	76.1 ± 10.3a	28.1 ± 0.8b	37.8 ± 4.9b	6.6 ± 0.8a	3.9 ± 0.5b	7.9 ± 1.3a
Litter
L1	3.85 ± 1.5a	4.22 ± 0.6a	5.49 ± 2.5a	3.84 ± 1.5a	4.82 ± 0.8a	5.41 ± 2.4a	127.3 ± 37.0a	112.4 ± 26.4a	138.4 ± 66.6a	7.1 ± 0.4a	6.0 ± 1.5a	5.8 ± 1.9a
L2		6.56 ± 0.8	7.24 ± 2.4		7.42 ± 0.7	8.21 ± 2.5		186.3 ± 23.8	199.0 ± 57.4		8.6 ± 1.2	7.2 ± 1.5
L3		11.94 ± 2.4	12.00 ± 0.7		14.39 ± 0.4	13.23 ± 0.7		385.5 ± 42.1	343.0 ± 9.8		13.8 ± 0.9	10.8 ± 0.3
Root
0–20 cm	6.97 ± 2.1a	4.25 ± 0.2a	5.75 ± 0.6a	9.31 ± 2.4a	6.35 ± 0.3a	7.59 ± 0.8a	191.4 ± 16.3a	158.8 ± 17.6a	225.4 ± 46.7a	9.0 ± 0.7a	7.8 ± 0.6a	9.0 ± 0.7a
20–50 cm	5.20 ± 0.5a	3.57 ± 0.3a	3.89 ± 0.4a	7.83 ± 0.9a	5.40 ± 0.5b	5.11 ± 0.4b	121.8 ± 13.3a	89.5 ± 3.4a	102.5 ± 16.3a	12.9 ± 0.5a	10.1 ± 1.7a	9.0 ± 0.8a
50–100 cm	4.93 ± 0.5a	3.47 ± 0.2b	3.94 ± 0.1ab	7.28 ± 0.6a	5.06 ± 0.1b	5.23 ± 0.1b	113.8 ± 3.2a	88.4 ± 8.4a	107.0 ± 13.4a	12.8 ± 0.2a	13.9 ± 0.2a	9.9 ± 1.8b
Soil
0–10 cm	14.89 ± 0.2a	16.62 ± 1.4a	16.77 ± 0.3a	26.20 ± 1.5a	24.49 ± 1.3a	23.40 ± 0.8a	319.5 ± 5.1a	338.4 ± 8.5a	324.9 ± 8.9a	7.4 ± 0.4a	12.6 ± 3.0a	11.3 ± 0.8a
10–20 cm	14.36 ± 0.3a	14.88 ± 0.4a	14.52 ± 0.5a	26.02 ± 2.3a	25.07 ± 2.9a	20.64 ± 1.0a	303.0 ± 10.4a	312.0 ± 3.3a	280.9 ± 15.4a	6.1 ± 0.6a	9.2 ± 1.7a	8.1 ± 0.9a
20–30 cm	13.36 ± 0.3a	14.34 ± 0.5a	13.52 ± 0.2a	26.17 ± 2.7a	20.87 ± 2.2a	22.25 ± 2.0a	288.9 ± 20.1a	274.2 ± 11.0a	288.2 ± 13.3a	4.6 ± 0.3a	8.2 ± 2.1a	7.2 ± 0.4a
30–50 cm	12.31 ± 0.4a	14.15 ± 1.0a	13.67 ± 0.2a	25.59 ± 2.8a	21.5 ± 1.8a	21.98 ± 1.8a	262.3 ± 10.0a	273.3 ± 16.1a	269.5 ± 6.4a	3.9 ± 0.7b	8.8 ± 2.2a	7.3 ± 0.1a
50–70 cm	13.07 ± 0.4a	14.15 ± 0.7a	13.36 ± 0.1a	27.89 ± 2.4a	25.14 ± 0.8a	20.45 ± 2.1b	288.8 ± 14.8a	308.4 ± 16.3a	277.8 ± 20.2a	5.0 ± 1.1a	8.4 ± 2.2a	6.3 ± 0.9a
70–100 cm	13.58 ± 0.2a	15.25 ± 0.3a	13.34 ± 0.1b	28.52 ± 0.9a	23.95 ± 1.4b	20.67 ± 0.3b	308.0 ± 11.7a	326.0 ± 17.3a	272.0 ± 4.5b	5.0 ± 0.3b	10.7 ± 1.2a	6.0 ± 0.7b

Note: L1, undecomposed litter; L2, incomplete decomposed litter; L3, complete decomposed litter. Lowercase letter in line indicates significant difference at 0.05 level among treatments (ANOVA).

The contents of trace elements in litter showed L3 > L2 > L1. The Fe and Al content of L1 at F18 was 9.6% and 25.5% higher than that at F0, respectively, whereas the Mn and B content was 11.7% and 15.5% lower than that at F0, respectively. The Fe, Al, and Mn content of L1 at F39 was 30.1%, 12.2%, and 23.1% higher than that at F18, respectively. The Fe, Al, and Mn content of L2 at F39 was 10.4%, 10.6%, and 6.8% higher than that at F18, respectively. The B content of L2 at F39 was 16.3% less than that at F18. The trace element contents of L3 at F39 were slightly lower than that at F18 (Table 2).

The Fe, Al, and Mn contents in the root in 0–20 cm were higher than that of 20–50 and 50–100 cm. However, B content in the root in 0–20 cm was less than that of 20–50 and 50–100 cm. The Fe, Al, Mn, and B content of root in 0–20 cm at F18 and was 39.0%, 31.8%, 17.0%, and 13.3% less than that at F0. The Fe, Al, Mn, and B content of the root in 0–20 cm soil at F39 was 35.3%, 19.5%, 41.9% and 15.4% higher than that at F18, respectively (Table 2).

The contents of Fe and B in each soil layer at F18 were increased, while the contents of Al was decreased. The content of Fe and B in 0–100 cm soil at F18 was 9.6% and 81.1% higher than that at F0, respectively. However, the content of Al was 12.1% less than that at F0. The Fe, Al, Mn, and B content in 0–100 cm soil at F39 was 4.7%, 8.3%, 6.5%, and 20.1% less than that at F18, respectively (Table 2).

Stocks Trace element stocks of green plant

The stock of Fe, Al, Mn, and B in green plant at F18 was 70.8%, 59.4%, 45.1%, and 12.9% lower than that at F0, respectively (p < .05). The B stock in green plant at F39 was 100.1% higher than that at F18 (p < .05; Figure 2).

FIGURE 2. The Fe, Al, Mn, and B stocks of green plant after long-term grazing exclusion. Lowercase letter indicated significant difference at 0.05 level (ANOVA). Error bars were one standard deviation.

Trace element stocks of root

The Fe, Al, and Mn mainly stocked in 0–20 cm root, accounting for 48.3%–63.1% of 0–100 cm root. The Fe, Al, Mn, and B stock in 0–20 cm root at F18 was 47.8%, 41.5%, 29.0%, and 25.8% lower than that at F0, respectively. The Fe, Al, Mn, and B stock in 0–20 cm root at F39 was 43.4%, 26.5%, 50.9%, and 22.6% higher than that at F18, respectively (Figure 3).

FIGURE 3. The Fe, Al, Mn, and B stocks of the root after long-term grazing exclusion. Lowercase letter indicated significant difference at 0.05 level (ANOVA). Error bars were one standard deviation.

Trace element stocks of litter

The stock of Fe, Al, Mn, and B in total litter at F18 was 52.6, 46.3, 58.2, and 33.5 times higher than that at F0. The Fe, Al, Mn, and B stock in L3 at F39 was 33.2%, 32.2%, 36.2% and 42.5% less than that at F18 (p < .05; Figure 4).

FIGURE 4. The Fe, Al, Mn, and B stocks in litter after long-term grazing exclusion. Lowercase letter indicated significant difference at 0.05 level (ANOVA). *p [less than] .05; **p [less than] .01; ns, no significance. Error bars were one standard deviation.

Trace element stocks of soil

The Fe stock in 70–100 cm soil at F18 was 9.13% higher than that at F0 (p < .05). The B stock in 30–50 cm soil and 70–100 cm soil at F18 was 122.8% and 108.6% higher than that at F0 (p < .05). The B and Mn stock in 70–100 cm soil at F39 was 45.2% and 18.8% less than that at F18, respectively (p < .05). The Al stock in 70–100 cm soil at F18 was 18.4% less than that at F0. The Al stock in 50–70 cm soil and 70–100 cm soil at F39 was 21.1% and 16.0% less than that at F18, respectively (Figure 5).

FIGURE 5. The Fe, Al, Mn, and B stocks in soil after long-term grazing exclusion. Lowercase letter indicated significant difference at 0.05 level (ANOVA). Error bars were one standard deviation.

Proportions of trace element stocks

The proportions of trace element stocks in the plant system at F18 were less than that at F0. The proportions of trace element stocks in the soil system at F18 were higher than that at F0. However, the proportions of trace element stocks in the plant system at F39 were higher than that at F18. The proportions of trace element stocks in the soil system at F39 were less than that at F18 (Table 3).

TABLE 3 The proportions of trace element stocks in grassland system after long-term grazing exclusion (Mean ± SE).

	Plant system proportion (%)	Soil system proportion (%)	Green plant proportion (%)	Root proportion (%)	Litter proportion (%)
					Total	L1	L2	L3
Fe
F0	0.55 ± 0.08a	99.45 ± 16.04a	0.08 ± 0.01a	99.83 ± 24.28a	0.10 ± 0.05c	0.10 ± 0.05b
F18	0.33 ± 0.02b	99.67 ± 15.48a	0.04 ± 0.02a	92.18 ± 23.82b	7.79 ± 0.55a	1.25 ± 0.49a	1.81 ± 0.09	4.73 ± 0.97
F39	0.45 ± 0.05b	99.55 ± 22.33a	0.03 ± 0.01a	94.73 ± 15.48b	5.24 ± 0.62b	1.52 ± 0.38a	1.20 ± 0.29	2.53 ± 1.07
Al
F0	0.60 ± 0.10a	99.40 ± 22.03a	0.06 ± 0.00a	99.88 ± 24.12a	0.07 ± 0.00b	0.07 ± 0.00b
F18	0.41 ± 0.12b	99.59 ± 18.14a	0.03 ± 0.02b	94.08 ± 18.57b	5.88 ± 0.66a	0.98 ± 0.12a	1.40 ± 0.57	3.50 ± 1.21
F39	0.48 ± 0.18a	99.52 ± 18.03a	0.03 ± 0.00b	95.67 ± 14.32b	4.31 ± 0.91a	1.14 ± 0.46a	1.04 ± 0.42	2.13 ± 0.74
Mn
F0	0.65 ± 0.24a	99.35 ± 3.13a	0.25 ± 0.09a	99.62 ± 8.49a	0.12 ± 0.08c	0.12 ± 0.08b
F18	0.49 ± 0.18b	99.51 ± 9.78a	0.18 ± 0.01b	92.52 ± 2.56b	7.30 ± 1.58a	1.07 ± 0.34a	1.66 ± 0.77	4.57 ± 1.23
F39	0.74 ± 0.37a	99.26 ± 2.15a	0.18 ± 0.07b	95.48 ± 2.33b	4.34 ± 1.24b	1.15 ± 0.28a	0.99 ± 0.12	2.20 ± 0.98
B
F0	2.68 ± 0.81a	97.32 ± 31.23a	0.30 ± 0.11b	99.60 ± 19.54a	0.09 ± 0.00b	0.09 ± 0.00a
F18	1.28 ± 0.19b	98.72 ± 28.93a	0.30 ± 0.08b	96.14 ± 23.56b	3.57 ± 0.55a	0.70 ± 0.03a	0.94 ± 0.18	1.94 ± 0.38
F39	1.67 ± 0.27b	98.33 ± 21.43a	0.64 ± 0.21a	96.71 ± 27.89b	2.65 ± 0.34a	0.84 ± 0.12a	0.62 ± 0.11	1.18 ± 0.27

Note: L1, undecomposed litter; L2, incomplete decomposed litter; L3, complete decomposed litter. Lowercase letter in row indicates significant difference at 0.05 level among treatments (ANOVA).

Compared with that at F0, the proportions of trace element stocks in litter at F18 were increased (especially in L3) in the plant system, and the proportions of them in the root were decreased. Compared with that at F18, the proportions of trace element stocks in litter at F39 were decreased from 3.57%–7.79% to 2.65%–5.24%, and the proportions of them stocks in the root were increased from 92.18%–96.14% to 94.73%–96.71%. After long-term grazing exclusion, the proportion of Fe stock in litter was the highest, and the proportions of B stocks in green plant and root were great.

Trace element reuse efficiencies

F18 obviously decreased the reuse efficiencies of Fe, Al, Mn, and B compared with F0. The reuse efficiency of B at F39 was obviously increased relative to F18 (Figure 6).

FIGURE 6. Trace element reuse efficiencies after long-term grazing exclusion.

Correlations of trace elements in green plant–litter–root–soil

The trace element relationship among green plant, litter, root, and soil were established (Table 4). The correlation values of Fe, Al, and Mn between the green plant and litter were significant (p < .01). The correlation value of Al between the root and litter was significant (p < .01). The correlation value of B content between the root and soil was significant (p < .01). The correlation value of B content between litter and soil was significant (p < .01).

TABLE 4 Green plant–litter–root–soil relationship (correlation) in respect to trace element contents as affected by long-term grazing exclusion.

	Fe		Al		Mn		B
	r	p	r	p	r	p	r	p
Green plant–root	.269	.484	.400	.286	.309	.418	−.225	.560
Green plant–litter	.813**	.008	.860**	.003	.839**	.005	.146	.708
Green plant–L1	.089	.820	.051	.896	.252	.513	.218	.574
Green plant–L2	.768*	.016	.739*	.023	.807**	.009	.133	.734
Green plant–L3	.665	.051	.801**	.010	.137	.725	.110	.978
Green plant–soil	.669*	.049	−.062	.873	.442	.234	−.038	.923
Root–litter	.584	.099	.671*	.048	.209	.590	.402	.283
Root–L1	−.465	.207	−.480	.191	−.175	.652	−.366	.333
Root–L2	.680*	.044	.776*	.014	.423	.257	.685*	.042
Root–L3	.609	.082	.670*	.048	−.173	.656	.015	.969
Root–soil	.217	.575	0.041	.917	.330	.386	.746*	.021
Litter–soil	.448	.226	.035	.929	.321	.399	.806**	.009
L1–soil	−.382	.310	−.557	.119	−.495	.175	.301	.431
L2–soil	.649	.590	.290	.449	.653	.057	.790*	.011
L3–soil	.201	.554	.019	.955	−.093	.786	.555	.076

* and ** indicates significant correlation at .05 and .01 level.

DISCUSSION The trace element shift from the plant via litter to soil during grazing exclusion 0–18 year

The study found that the proportions of trace element stocks in soil with 18-year grazing exclusion were increased relative to grazing, which suggested that the trace elements might shift from plant to soil. In the plant system, we found that 18-year grazing exclusion decreased the proportions of trace elements in green plant and root, whereas greatly increased them in litter. This indicated that the trace elements might shift from the plant via litter to soil during grazing exclusion 0–18 year. These variations of distributions of trace elements in plant–litter–soil might because of the variations of vegetation productivity (Cheng et al., 2016; Mekuria et al., 2007; Qasim et al., 2017), soil physical–chemical properties (Zeng et al., 2017), and mineral nutrients of soil (Dai et al., 2021; Hu et al., 2020). Long-term grazing exclusion could increase the biomass of green plant owing to the reduction of livestock consumption by grazing animal, and the improvement of water holding capacity of soil by high plant coverage and low soil bulk density The large amount of plant in long-term grazing exclusion plot caused great litter accumulation. In further, the decomposition of litter caused the increase of trace element stocks in soil.

The stocks of Fe, Al, and Mn in green plant were significantly decreased with 18 year grazing exclusion because of the great reduction of trace element contents. This might be attributed to a dilution effect of largely increased vegetation productivity. The increase of green plant biomass of long-term grazing exclusion was directly related to the decreased livestock consumption by grazing animals (Alberti et al., 2017; Steffens et al., 2008), as well as the improvement of soil physical–chemical properties and soil nutrients. The growth of the root was depended by variations of productivity and compositions of above-ground community and soil physical–chemical properties. The stocks of Fe, Al, Mn, and B in the root with 18-year grazing exclusion were decreased because of the reductions of root biomass and trace element contents. Long-term grazing exclusion can inhibit photosynthesis of plant because of the light restriction caused by the excess litter (Liu et al., 2019; Zhang et al., 2019). Therefore, this can reduce the allocation of photosynthetic product into the root, leading to an increase in the root mortality (Chen et al., 2006). Litter decomposition is the main way of nutrient return from plant to soil. It is of great importance for maintaining the balance of ecosystem (Ball et al., 2014; Ren et al., 2016). The study showed that the stocks of Fe, Al, Mn, and B in litter were significantly increased with 18-year grazing exclusion. This attributed to the increases of litter biomass and trace element contents. The nutrients will be transferred and retained in plant before the plant withering, which is called nutrient resorption (Aerts, 1996; Berg, 1986; Han et al., 2005; Millett et al., 2010). The results found that the reuse efficiencies of trace elements with 18-year grazing exclusion were greatly lower than that with 0-year grazing. This indicated that the increases of trace element contents in litter might be mainly originated from the green plant. The significant relationships of Fe, Al, and Mn contents between green plant and litter confirmed this viewpoint. The contents of Fe and Al in undecomposed litter were increased with 18-year grazing exclusion, while the contents of Mn and B in undecomposed litter were decreased. This attributed to the higher mobility in phloem of Mn and B, as well as reuse degree (Zhao et al., 2004). This also indicated that Fe and Al had poor mobility in phloem, and Fe and Al accumulated in litter rarely transferred to the below-ground part. The above results indicated that most trace elements were accumulated in litter from plant, especially from root. Further, the contents of trace elements in soil were mainly depended on the litter decomposition. The study showed that the stocks of Fe, Mn, and B in 0–100 cm soil were increased with 18-year grazing exclusion, while the stock of Al was obviously decreased. This was mainly because of the contents of trace elements in soil. The content of Al³⁺ in soil in a semi-arid region in Brazil was decreased with grazing exclusion (Oliveira Filho et al., 2019). The Fe and Mn contents in soil were increased in the warm steppe with 29-year grazing exclusion and in the alpine meadow steppe with 24-year grazing exclusion (Li et al., 2011). The contents of Fe, B, and Mn in the same region of this study were increased with 13-year grazing exclusion (He, 2019). The plant coverage and litter accumulation on the soil surface were increased by long-term grazing exclusion. This reduced the risks of soil nutrients loss caused by wind and water erosion (García et al., 2013; Hoffmann et al., 2008). Many studies found that the pH value was significantly decreased with long-term grazing exclusion (Bai et al., 2021; Pei et al., 2008). This resulted in the increase in rock weathering and the release of trace elements into soil (Bowman et al., 2008). Among these four trace elements, the B content in soil with long-term grazing exclusion was increased most. The large amounts of B in soil were shifted from the root and litter because of the high mobility in phloem of B. The significant relationships of B contents between litter and soil (r = .806**), and between the root and soil (r = .746*) verified this explanation. However, the study found that the Al content in soil was decreased with long-term grazing exclusion. The Al contents in litter were significantly related to green plant (r = .860**) and root (r = .670*). This showed that most Al originated from green plant and root was accumulated in litter, and was difficultly to return into soil due to the poor mobility in phloem.

The trace element shift from the litter via soil to plant during grazing exclusion 18–39 year

Continue grazing exclusion for 39 years obviously increased the biomass of root and undecomposed litter, while significantly decreased the biomass of incomplete-, and complete decomposed litter compared with 18-year grazing exclusion (Table 1). Therefore, continue grazing exclusion for 39 years further altered the distributions of trace elements in plant–root–litter–soil relative to 18-year grazing exclusion. The study found that grazing exclusion for 39 years decreased the proportions of trace element stocks in soil compared with 18-year grazing exclusion, which suggested that the trace element shifted from soil to plant. In plant system, we found that 39-year grazing exclusion obviously decreased the proportions of trace elements in litter, whereas increased them in green plant and root. This indicated that the trace elements might shift from the litter via soil to plant during grazing exclusion 18–39 year. The decreases of trace element stocks in litter were mainly resulted from the reductions of incomplete- and complete decomposed litter biomass after continue grazing exclusion for 39 years. In the course of time, continue grazing exclusion for 39 years was in favor of the litter decomposition, and promoted more elements into soil for absorption by root.

The Fe and Mn contents in 0–40 cm soil in grassland with 33-year grazing exclusion were less than that with 13-year grazing exclusion in the same region of this study (He, 2019). We also found that the stocks and contents of Fe, Al, Mn, and B in 0–100 cm soil with 39-year grazing exclusion were significantly less than that with 18-year grazing exclusion. The Fe and Mn contents and stocks in the root were significantly increased with 39-year grazing exclusion, especially in 0–20 cm soil. This might be attributed to the optical compensation effect of restoring the above-ground plants. Large amounts of undecomposed litter might inhibit the establishment of seedling and restrict the productivity of vegetation (Hovstad & Ohlson, 2008; Loydi et al., 2013; Ruprecht & Szabó, 2012). Therefore, more photosynthetic products might be distributed to the root to restore the growth of above-ground plant. Thus, most trace elements in soil could be absorbed by root. The decomposition rate of litter was strongly dependent on the Mn content because Mn is a key component of lignin decomposing enzymes at the late stage of decomposition (Berg et al., 2007; Tao et al., 2018; Trum et al., 2015; Whalen et al., 2018). The higher the content of Mn, the faster the decomposition of litter (Keiluweit et al., 2015). The Mn content (112.46 mg/kg increased to 138.41 mg/kg) with 39-year grazing exclusion was higher than that with 18-year grazing exclusion. This explored that grazing exclusion for 39 years promoted the decomposition of undecomposed litter. This further explored that over grazing exclusion for 39 year decreased the proportions of trace elements in litter, while made more trace elements distributed in root.

Ecological significance as affected by long-term grazing exclusion

The deficiency or toxicity of trace elements limits the productivity of plants, and results in enormous economic losses to the herders (Xin et al., 2011; Yadav, 2010). The mean range for Mn content in grass was 71–127 mg/kg (Kabata-Pendias & Mukherjee, 2007). The Mn content in green plant was decreased from 76.06 mg/kg to 28.14–37.80 mg/kg with 18- and 39-year grazing exclusion. This might cause the deficiency of Mn. The Fe content in the plant was 25–500 mg/kg (Hennessy et al., 2020). The Fe content in the green plant was decreased from 1300 mg/kg to 180–200 mg/kg with 18- and 39-year grazing exclusion. This explored that Fe toxicity occurred in grassland with long-term grazing, and the deficiency of Mn occurred in grassland with long-term grazing exclusion. The B content in green plant was changed from 6.62 mg/kg to 3.89–7.94 mg/kg in grassland with 18- and 39-year grazing exclusion. This was insufficient to meet ruminant dietary requirement of 35–40 mg/kg (Fisher, 2008; Suttle, 2009). In addition, the B stock in green plant was greatly increased with 39-year grazing exclusion because of a great increase of B content compared with 18-year grazing exclusion. This indicated that the effective of B resorption in the plant played an important role in the change of B content rather than the dilution effect of long-term grazing exclusion. B can be transferred from mature or senescent leaves to young organs for reuse when B content in soil is low (Liu et al., 2011). Therefore, lots of B accumulated in green plant and less of B in litter. Less content and stock of B in the root with 39-year grazing exclusion were observed relative to 18-year grazing exclusion. This indicated that B was rapidly shifted from the root to the green plant because of the high mobility in phloem and reuse.

CONCLUSION

The contents and stocks of trace elements in green plant, litter, root, and soil in grassland with long-term grazing exclusion were investigated for the first time in Inner Mongolia. The Fe toxicity occurred in the grassland with long-term grazing, and Mn deficiency was observed in the grassland with long-term grazing exclusion. We confirmed our hypothesis that the distributions of trace elements in grassland system were altered with different years of long-term grazing exclusion. The trace elements were mainly shifted from the green plant and root to soil and litter with 18-year grazing exclusion. However, the trace elements were mainly shifted from soil and complete decomposed litter to root with continue 39-year grazing exclusion compared with grazing exclusion for 18 years. The complete decomposed litter played an important role in the relationship of trace elements between litter and soil. Moreover, the results found that over long-term grazing exclusion caused the accumulation of trace elements in the root.

AUTHOR CONTRIBUTIONS

Juan Hu: Investigation (equal); writing – original draft (equal). Qiang Li: Investigation (equal). Yingxin Huang: Writing – review and editing (equal). Qilin Zhang: Data curation (equal). Daowei Zhou: Conceptualization (equal); funding acquisition (equal).

ACKNOWLEDGMENTS

This research was supported by the Strategic Priority Research Program of the Chinese Academy of Sciences (Grant No. XDA28110202), and the Open Research Fund of Key Laboratory of Mollisols Agroecology, Northeast Institute of Geography and Agroecology, Chinese Academy of Sciences (2020ZKHT-04), and the Special Fund Project of Jilin Province and Chinese Academy of Sciences (2021SYHZ0003).

CONFLICT OF INTEREST

No potential competing interest was reported by the authors.

DATA AVAILABILITY STATEMENT

The data that support the findings of this study are openly available in [Dryad Data Juan Hu] at https://doi.org/10.5061/dryad.5qfttdz7r.