Demand-Supply Balance of the Nitrogen Nutrients Converted from Regional Agricultural Organic Wastes for Agricultural Utilization

Demand-Supply Balance of the Nitrogen Nutrients Converted from Regional Agricultural Organic Wastes for Agricultural Utilization

Qingsheng ZhouKaige Qu Yangzi Zhang Jie Deng Wanjing Wang 

School of Geography and Tourism, Zhengzhou Normal University, Zhengzhou 450044, China

College of Materials and Environmental Engineering, Hangzhou Dianzi University, Hangzhou 310018, China

Henan Institute of Economics and Trade, Zhengzhou 450018, China

College of Resources and Environment, Yunnan Agricultural University, Kunming 650201, China

Corresponding Author Email: 
zhou1166@zznu.edu.cn
Page: 
813-819
|
DOI: 
https://doi.org/10.18280/ijdne.150606
Received: 
11 June 2020
|
Revised: 
23 September 2020
|
Accepted: 
3 October 2020
|
Available online: 
26 December 2020
| Citation

© 2020 IIETA. This article is published by IIETA and is licensed under the CC BY 4.0 license (http://creativecommons.org/licenses/by/4.0/).

OPEN ACCESS

Abstract: 

To promote the recycling of agricultural organic wastes (AOWs), e.g., crop straws, and livestock and poultry (LP) manures, it is very important to analyze the demand-supply balance of the nitrogen nutrients converted from AOWs for agricultural utilization on a regional basis. Focusing on Shangshui County in central China’s Henan Province, this paper thoroughly analyzes this demand-supply balance through literature query and field survey. Firstly, the amount of nitrogen nutrients converted from the crop straws, and LP manures were calculated for the study area. Next, the demand for nitrogen nutrients of agricultural planting in the study area was estimated based on the soil properties and agricultural planting area. Based on the calculation results, the demand-supply balance of the nitrogen nutrients converted from AOWs for agricultural utilization in the study area was subject to quantitative analysis. The results show that: In 2017, the agricultural planting in Shangshui County demanded 35.16 kilotons of nitrogen nutrients; the total supply of nitrogen nutrients converted from AOWs stood at 25.86 kilotons, including 12.41 kilotons from crop straws (47.99%) and 13.45 kilotons (52.01%) from LP manures; the demand-supply ratio (amount of demand/supply quantity) of nitrogen nutrients was 1.36, that is, the demand surpassed the supply; therefore, the nitrogen nutrients provided by the AOWs in the study area can be fully utilized by the agricultural soil in the region.

Keywords: 

agricultural organic wastes (AOWs), livestock and poultry (LP) manures, crop straws, nitrogen nutrients, demand-supply balance

1. Introduction

In recent years, a growing attention has been paid to circular agriculture. One of the important strategies for the development of circular agriculture is the land reduction of agricultural organic wastes (AOWs) [1, 2]. Despite its importance, the efficient utilization of AOWs has not been realized in many regions [3, 4].

The concept of zero waste, proposed by Paul Palmer in 1973, did not attract widespread attention until the late 1990s. The core of zero waste is to redefine the value of waste, and recognize waste as a potential resource. So far, many countries have laid down policies to reduce the landfill and incineration of waste [5, 6]. The most effective reduction method is source reduction and recycling [7, 8].

Livestock and poultry (LP) manures and crop straws, as major AOWs [9], have been the focal points in recycling. Many scholars have explored the recycling methods [10, 11] and utilization technologies [12-14] of these AOWs. Currently, AOWs are mostly recycled by composting [15, 16] and biogas fermentation [17, 18]. Recycling through composting has the minimum impact on the environment [19, 20].

The rapid growth of China’s economy is accompanied by continued increase in the per-capita emissions of AOWs in rural areas, which is higher than that in any other development countries [21]. This severely threatens the sustainability of the rural environment. In the traditional agricultural economy of China, AOWs are usually used as feed (crop straws) or compost (LP manures, and crop straws). Only a small number of AOWs is discharged into the environment.

With the burgeoning social economy in rural areas, the ability to recycle AOWs has declined sharply, and the rural environment has been seriously impacted by the heavy emissions of AOWs [4]. China is a large agricultural country with abundant sources of crop straws [22]. At present, more than 700 million tons of crop straws is produced every year. However, the crop straws have not been utilized comprehensively. Many of them are disposed of in environmentally unfriendly ways, such as random littering and incineration [23].

Meanwhile, the boom of China’s animal husbandry has brought lots of LP manures, creating a major source of pollution. Each year, the LP industry produces 2.43×108t of manures. Without being decomposed, these manures are directly applied to farmland, which not only harm crops, but also pollute surface water and groundwater. The severity and scope of environmental pollution that ensures far exceed those of industrial pollution and urban sprawl [24].

There are about 4,100 organic fertilizer manufacturers in China, producing about 50 million tons of compost each year. However, the production merely consumes 2.6% of the annual generation of AOWs (http://www.cnfert.com/). Against this backdrop, it is of great significance to recycle AOWs such as crop straws and LP manures [25]. The recycling can efficiently convert materials and circulate energy in the agricultural production system, and promote environment protection and circular agriculture [26].

The early research has greatly contributed to the recycling of AOWs. This paper holds that the success of the recycling strategy for AOWs hinges on the effective utilization of the recycled materials. It is also important to mine the demand for the materials recycled from AOWs, and grasp the possibility of their supply.

This paper mainly discusses the demand-supply balance of the nitrogen nutrients converted from regional AOWs for agricultural utilization. Firstly, the calculation formulas were derived for the supply of nitrogen nutrients converted from regional AOWs, and the demand for nitrogen nutrients of agricultural planting. Next, the said demand-supply balance was modeled for analysis. Finally, an empirical analysis was conducted on Shangshui County in central China’s Henan Province. The research findings lay a scientific basis for the recycling of AOWs in the region.

2. Methodology

This paper mainly studies the demand-supply balance in the nitrogen nutrients converted from AOWs in 9 towns, 11 townships, 1 farm, and 3 subdistrict offices of Shangshui County, namely, Huangzhai Town, Lianji Town, Weiji Town, Guqiang Town, Baisi Town, Bacun Town, Tanzhuang Town, Dengcheng Town, Huji Town, Chengguan Township, Pingdian Township, Yuanlao Township, Huahe Township, Yaoji Township, Shuzhuang Township, Dawu Township, Zhangming Township, Haogang Township, Zhangzhuang Township, Tangzhuang Township, Shangshui County Farm, Xincheng Subdistrict Office, Laocheng Subdistrict Office, and Dongcheng Subdistrict Office.

The amounts of nitrogen nutrients converted from crop straws and LP manures were calculated for each region. Considering the soil properties of the study area, the demand for nitrogen nutrients of agricultural soil in each region. Based on these calculation results, the demand-supply balance of nitrogen nutrients was analyzed quantitatively, providing a scientific reference of the recycling of AOWs in the study area.

3. Calculation of Demand and Supply

3.1 Demand calculation

The demand for nitrogen nutrients Pij in each region was calculated by multiplying the planting area of each crop Sij with the reference demand for nitrogen nutrients Dj of each crop:

$P_{i j}=S_{i j} \times D_{j}$     (1)

where, Pij is the demand for nitrogen nutrients (kiloton/year); Sij is the planting area of each crop (thousand hectares/year); Dj is the reference demand for nitrogen nutrients of each crop (kiloton/ thousand hectares); j is the serial number of crops; i is the serial number of regions in the study area.

The planting area of each crop was obtained from relevant statistical yearbooks [27]. The reference demand for nitrogen nutrients of each crop was extracted from related literature [28] (Table 1).

Table 1. The reference demand for nitrogen nutrients of each crop (kiloton/ thousand hectares)

Crop

Wheat

Corn

Beans

Sweet potato

Peanut

Sesame

Sugar cane

Fruits and melons

Vegetables

Reference demand

0.074

0.113

0.015

0.20

0.15

0.15

0.12

0.22

0.25

Table 2. The demand for nitrogen nutrients of each crop in each region of the study area in 2017 (kiloton)

Crop

Wheat

Corn

Beans

Sweet potato

Peanut

Xincheng Subdistrict Office

0.0143

0.0147

0.0009

0.0100

0.0009

Dongcheng Subdistrict Office

0.0531

0.0811

0.0000

0.0000

0.0000

Laocheng Subdistrict Office

0.0484

0.0781

0.0000

0.0000

0.0000

Huangzhai Town

0.2909

0.4130

0.0053

0.0130

0.0030

Lianji Town

0.1628

0.4139

0.0000

0.0000

0.0000

Weiji Town

0.2871

0.1765

0.0212

0.0220

0.0000

Guqiang Town

0.4113

0.5138

0.0078

0.0182

0.0123

Baisi Town

0.2355

0.2406

0.0232

0.0528

0.1212

Bacun Town

0.3108

0.4896

0.0018

0.0146

0.0090

Tanzhuang Town

0.3929

0.4462

0.0075

0.0378

0.0327

Dengcheng Town

0.3053

0.2921

0.0138

0.0381

0.0882

Huji Town

0.2658

0.1718

0.0161

0.0270

0.0419

Chengguan Township

0.1334

0.0953

0.0088

0.0458

0.0350

Pingdian Township

0.2594

0.3013

0.0100

0.0568

0.0152

Yuanlao Township

0.2580

0.1099

0.0209

0.1000

0.0240

Huahe Township

0.2302

0.1526

0.0116

0.0282

0.0254

Yaoji Township

5.5127

5.0161

0.4470

0.0000

0.0465

Shuzhuang Township

0.2915

0.3597

0.0046

0.0112

0.0542

Dawu Township

0.2913

0.4449

0.0000

0.0000

0.0000

Zhangming Township

0.3042

0.3894

0.0003

0.0186

0.0858

Haogang Township

0.2466

0.2410

0.0000

0.0666

0.0600

Zhangzhuang Township

0.3898

0.5258

0.0007

0.0026

0.0027

Tangzhuang Township

0.2351

0.1935

0.0175

0.0150

0.0120

Shangshui County Farm

0.0730

0.0662

0.0042

0.0001

0.0001

Total

11.0035

11.2270

0.6232

0.5784

0.6698

Crop

Sesame

Sugar cane

Fruits and melons

Vegetables

Sum

Xincheng Subdistrict Office

0.0000

0.0000

0.0004

0.0085

0.0498

Dongcheng Subdistrict Office

0.0000

0.0000

0.0000

0.1580

0.2923

Laocheng Subdistrict Office

0.0000

0.0000

0.0176

0.1445

0.2886

Huangzhai Town

0.0033

0.0000

0.0133

0.0931

0.8349

Lianji Town

0.0000

0.0000

0.0000

0.1248

0.7015

Weiji Town

0.0926

0.0000

0.0015

0.0759

0.6768

Guqiang Town

0.0171

0.0000

0.0009

0.0568

1.0382

Baisi Town

0.1212

0.0000

0.0103

4.4285

5.2334

Bacun Town

0.0000

0.0000

0.1100

0.2488

1.1846

Tanzhuang Town

0.0779

0.0000

0.0781

1.8785

2.9517

Dengcheng Town

0.0065

0.0000

0.0108

0.1165

0.8712

Huji Town

0.0578

0.0000

0.0171

0.0954

0.6928

Chengguan Township

0.0269

0.0264

0.0125

0.2925

0.6765

Pingdian Township

0.0600

0.0000

0.0505

0.2661

1.0191

Yuanlao Township

0.0554

0.0000

0.0090

0.0400

0.6173

Huahe Township

0.0066

0.0128

0.0128

0.0458

0.5258

Yaoji Township

0.0000

0.0000

0.0310

0.2960

11.3493

Shuzhuang Township

0.0000

0.0000

0.0671

0.0359

0.8242

Dawu Township

0.0000

0.0000

0.0103

0.2288

0.9753

Zhangming Township

0.0000

0.0000

0.0231

0.0330

0.8544

Haogang Township

0.0000

0.0000

0.0059

0.1863

0.8065

Zhangzhuang Township

0.0008

0.0000

0.1791

0.9483

2.0496

Tangzhuang Township

0.0047

0.0000

0.0075

0.0175

0.5027

Shangshui County Farm

0.0002

0.0000

0.0000

0.0000

0.1437

Total

0.5307

0.0392

0.6689

9.8192

35.1599

Among the regions, Yaoji Township raised the largest demand for nitrogen nutrients: 11.35 kilotons (32.28%), owing to the large planting area of crops. Meanwhile, Xincheng Subdistrict Office had the least demand: 0.05 kiloton (0.14%), due to the small planting area of crops in the residential areas.

According to the data in Table 1 and the planting area of each crop, the demand for nitrogen nutrients of each crop in each region of the study area was obtained by formula (1). As shown in Table 2, The total demand for nitrogen nutrients of crops in the study area was 35.16 kilotons. Wheat, corn, and vegetables had the highest demands: 11.00 kilotons (31.29%), 11.23 kilotons (31.94%), and 9.82 kilotons (27.93%), respectively. This is mainly attributable to the large planting area of wheat and corn, and the high reference demand for nitrogen nutrients of vegetables. By contrast, sugar cane had the least demand of 0.04 kiloton (0.11%), mainly because of the small planting area.

3.2 Supply calculation

3.2.1 Nitrogen nutrients content of crops

The nitrogen nutrients content of each crop was calculated in two steps. First, the straw amount Wij of each crop was calculated by multiplying the crop yield Hij with the grain-to-straw ratio Rij of that crop:

$W_{i j}=\sum\left(H_{i j} \times R_{j j}\right)$      (2)

where, Wij is the straw amount of each crop (kiloton); Hij is the crop yield (kiloton); Rij is the grain-to-straw ratio of each crop; j is the serial number of AOWs; i is the serial number of regions in the study area.

Next, the nitrogen nutrients content Cij of each crop was calculated by multiplying the straw amount Wij of the crop with the percentage of nitrogen in crop straw Nij:

$C_{i j}=W_{i j} \times N_{i j}$      (3)

where, Cij is the nitrogen nutrients content of each crop (kiloton); Wij is the straw amount of each crop (kiloton); Nij is the percentage of nitrogen in crop straw of each crop; j is the serial number of AOWs; i is the serial number of regions in the study area.

The yield of each crop was obtained from relevant statistical yearbooks [27]. The grain-to-straw ratio and percentage of nitrogen in crop straw of each crop were extracted from related literature [28, 29] (Table 3).

According to the data in Table 3 and data from the statistical yearbooks, the total amount of nitrogen nutrients converted from crop straws in the study area was obtained by formulas (2) and (3) as 12.41 kilotons in 2017. Wheat and corn contributed 85.31% of the total amount. Among the various regions, Guqiang Town produced the largest amount of nitrogen nutrients: 0.92 kiloton (7.41%).

3.2.2 Nitrogen nutrients content of LP manures

The nitrogen nutrients content of each LP manure was also calculated in two steps. First, the amount of each LP manure Fij was calculated by multiplying the number of each LP Yij with the daily excretion coefficient Eij of the LP, and the feeding period Tij of that LP:

$F_{i j}=\Sigma\left(Y_{i j} \times E_{i j} \times T_{i j}\right)$     (4)

where, Fij is the amount of each LP manure (kiloton); Yij is the number of each LP (each); Eij is the daily excretion coefficient of each LP; Tij is the feeding period of each LP; j is the serial number of the LPs; i is the serial number of regions in the study area.

Next, the nitrogen nutrients content Bij of each LP manure was calculated by multiplying the amount of each LP manure Fij with the percentage of nitrogen in that LP manure:

$B_{i j}=F_{i j} \times M_{i j}$      (5)

where, Bij is the nitrogen nutrients content of each LP manure (kiloton); Fij is the amount of each LP manure (kiloton); Mij is the percentage of nitrogen in each LP manure; j is the serial number of the LPs; i is the serial number of regions in the study area.

The number of each LP was obtained from relevant statistical yearbooks [27]. The daily excretion coefficient of each LP and percentage of nitrogen in each LP manure were extracted from related literature [28, 29] (Table 4).

According to the data in Table 4 and data from the statistical yearbooks, the total amount of nitrogen nutrients converted from LP manures in the study area was obtained by formulas (4) and (5) as 13.45 kilotons. Among them, pig manures contributed the greatest portion of nitrogen nutrients: 30.71% (4.13 kilotons).

Table 3. The grain-to-straw ratio and percentage of nitrogen in crop straw of each crop

Crop

Wheat

Corn

Beans

Sweet potato

Peanut

Sesame

Grain-to-straw ratio

1.2

1.34

1.60

0.5

0.8

0.17

Percentage of nitrogen

0.65

0.92

1.81

2.37

1.82

1.31

Table 4. The daily excretion coefficient of each LP and percentage of nitrogen in each LP manure

LP type

Breeder pig

Market pig

Beef cattle

Dairy cow

Sheep

Rabbit

Poultry

Total

Daily excretion coefficient (kg/each)

3.30

2.10

18.00

45.50

2.10

0.16

0.13

71.29

Percentage of nitrogen

0.55

0.55

0.38

0.38

1.01

0.87

1.03

4.77

3.2.3 Supply of nitrogen nutrients

The supply of nitrogen nutrients Qij in each region was calculated by adding up the nitrogen nutrients content Cij of every crop straw and that Bij of every LP manure:

$Q_{i j}=C_{i j}+B_{i j}$      (6)

where, Qij is the supply of nitrogen nutrients in each region (kiloton); Cij is the nitrogen nutrients content of each crop straw (kiloton); Bij is the nitrogen nutrients content of each LP manure (kiloton); j is the serial number of AOWs; i is the serial number of regions in the study area.

By formula (6), the supply of nitrogen nutrients converted from AOWs in each region of the study area was obtained (Table 5). It can be seen that the total supply of nitrogen nutrients converted from AOWs stood at 25.86 kilotons, including 12.41 kilotons from crop straws (47.99%) and 13.45 kilotons (52.01%) from LP manures. The amounts of nitrogen nutrients from the two sources were similar in scale.

Table 5. The supply of nitrogen nutrients converted from AOWs in each region of the study area in 2017 (kiloton)

 

Nitrogen nutrients from crop straws

Nitrogen nutrients from LP manures

Total supply of nitrogen nutrients

Xincheng Subdistrict Office

0.0657

0.0732

0.1389

Dongcheng Subdistrict Office

0.1344

0.1072

0.2416

Laocheng Subdistrict Office

0.1003

0.0741

0.1744

Huangzhai Town

0.6702

0.6392

1.3094

Lianji Town

0.0389

0.6829

0.7218

Weiji Town

0.5918

0.7326

1.3244

Guqiang Town

0.9171

1.2148

2.1319

Baisi Town

0.7363

0.6420

1.3783

Bacun Town

0.7373

0.6549

1.3923

Tanzhuang Town

0.8158

0.8482

1.6640

Dengcheng Town

0.7043

0.5885

1.2929

Huji Town

0.5378

0.6136

1.1514

Chengguan Township

0.2903

0.5987

0.8890

Pingdian Township

0.6022

0.6136

1.2158

Yuanlao Township

0.4918

0.5804

1.0722

Huahe Township

0.4235

0.5109

0.9345

Yaoji Township

0.6271

0.5752

1.2023

Shuzhuang Township

0.6686

0.7636

1.4322

Dawu Township

0.6538

0.6892

1.3430

Zhangming Township

0.7472

0.4860

1.2332

Haogang Township

0.4270

0.5149

0.9419

Zhangzhuang Township

0.7461

0.6808

1.4269

Tangzhuang Township

0.5094

0.5103

1.0198

Shangshui County Farm

0.1742

0.0565

0.2307

Total

12.4112

13.4513

25.8626

4. Demand-Supply Balance Analysis

Table 6 and Figure 1 illustrate the demand-supply ratio (amount of demand/supply quantity) of nitrogen nutrients converted from AOWs in each region of the study area in 2017.

As shown in Table 6 and Figure 1, in 2017, the total amount of nitrogen nutrients converted from AOWs in the study area reached 25.86 kilotons, while the total demand for nitrogen nutrients in the study area was 35.16 kilotons. Thus, the supply-demand ratio of nitrogen nutrients was 1.36. This means the supply falls short of demand. The short supply is the results of the large area of agricultural planting in the study area, which requires lots of nitrogen nutrients, and the relatively insufficient supply of nitrogen nutrients from AOWs.

In addition, the demand-supply ratios of Yaoji Township, Tanzhuang Town, Laocheng Subdistrict Office, Zhangzhuang Town, and Dongcheng Subdistrict Office were 9.44, 1.77, 1.65, 1.44, and 1.21, respectively. The greater-than-1.0 ratios indicate that the planting industry is highly developed in these regions. The demand-supply ratios in all the other regions were below 1.0. The lowest ratios were observed in Xincheng Subdistrict Office (0.36), Tangzhuang Township (0.49), and Guqiang Town (0.49). This is attributable to their close proximity to the downtown, limited area of farmlands, and mature LP breeding.

Table 6. The demand-supply ratio of nitrogen nutrients converted from AOWs in each region of the study area in 2017 (kiloton)

 

Supply of nitrogen nutrients

Demand of nitrogen nutrients

Demand-supply ratio

Xincheng Subdistrict Office

0.0498

0.1389

0.36

Dongcheng Subdistrict Office

0.2923

0.2416

1.21

Laocheng Subdistrict Office

0.2886

0.1744

1.65

Huangzhai Town

0.8349

1.3094

0.64

Lianji Town

0.7015

0.7218

0.97

Weiji Town

0.6768

1.3244

0.51

Guqiang Town

1.0382

2.1319

0.49

Baisi Town

5.2334

1.3783

3.80

Bacun Town

1.1846

1.3923

0.85

Tanzhuang Town

2.9517

1.6640

1.77

Dengcheng Town

0.8712

1.2929

0.67

Huji Town

0.6928

1.1514

0.60

Chengguan Township

0.6765

0.8890

0.76

Pingdian Township

1.0191

1.2158

0.84

Yuanlao Township

0.6173

1.0722

0.58

Huahe Township

0.5258

0.9345

0.56

Yaoji Township

11.3493

1.2023

9.44

Shuzhuang Township

0.8242

1.4322

0.58

Dawu Township

0.9753

1.3430

0.73

Zhangming Township

0.8544

1.2332

0.69

Haogang Township

0.8065

0.9419

0.86

Zhangzhuang Township

2.0496

1.4269

1.44

Tangzhuang Township

0.5027

1.0198

0.49

Shangshui County Farm

0.1437

0.2307

0.62

Total

35.1599

25.8626

1.36

Figure 1. The demand-supply ratio of nitrogen nutrients converted from AOWs in each region of the study area in 2017 (kiloton)

5. Conclusions

Through literature query and field survey, this paper analyzes the demand-supply balance in the nitrogen nutrients converted from AOWs in 9 towns, 11 townships, 1 farm, and 3 subdistrict offices of Shangshui County. Firstly, the demand for nitrogen nutrients was derived from the planting area, and reference demand for nitrogen nutrients of each crop in the study area. Then, the supply of nitrogen nutrients of each crop was calculated based on its straw amount and grain-to-straw ratio; the supply of nitrogen nutrients of each LP manure was computed based on the number of each LP, as well as the daily excretion coefficient, and nitrogen nutrients content of each LP manure.

Through the calculations, the total demand for nitrogen nutrients in 2017 of the study area was 35.16 kiloton, while the total supply of nitrogen nutrients converted from AOWs stood at 25.86kiloton, including 12.41 kilotons from crop straws (47.99%) and 13.45 kilotons (52.01%) from LP manures. The demand-supply ratio (amount of demand/supply quantity) was 1.36, indicating that the AOWs (crop straws, and LP matures) in the study area cannot fully satisfy the demand for nitrogen nutrients in the region.

Acknowledgements

This work was supported by the Key Special (Soft Science) Project for Research and Development (R&D) and Promotion of Henan Province, 2021 (Grant No.: 212400410071), the Preferential Scientific Research Projects for Overseas Students, Human Resources and Social Security Department, Henan Province, China (Grant No.: [2019] 82), the Oriented Research Bidding Project of Zhengzhou Normal University (Second Batch), and the Special Fund for Scientific Research Startups of Zhengzhou Normal University.

  References

[1] Zhou, Q.S., Wang, Y., Zhang, Y.C., Li, X.Z. (2018). Analysis on supply-demand balance of compost from agricultural organic wastes in Henan Province, China. Chemical Engineering Transactions, 64: 55-60. https://doi.org/10.3303/CET1864010

[2] Mouri, G., Aisaki, N. (2015). Using land-use management policies to reduce the environmental impacts of livestock farming. Ecological Complexity, 22: 169-177. http://dx.doi.org/10.1016/j.ecocom.2015.03.003

[3] Zhou, Q., Li, X., Yang, C., Zhao, Y. (2018). Demand-supply balance analysis of agricultural organic waste recycling in Northern Henan Province, China. Polish Journal of Environmental Studies, 27(5): 2367-2376. https://doi.org/10.15244/pjoes/79818

[4] Zeng, C., Niu, D., Zhao, Y. (2015). A comprehensive overview of rural solid waste management in China. Frontiers of Environmental Science & Engineering, 9(6): 949-961. https://doi.org/10.1007/s11783-015-0816-8

[5] Olay-Romero, E., Turcott-Cervantes, D.E., del Consuelo Hernández-Berriel, M., de Cortázar, A.L.G., Cuartas-Hernández, M., de la Rosa-Gómez, I. (2020). Technical indicators to improve municipal solid waste management in developing countries: A case in Mexico. Waste Management, 107: 201-210. https://doi.org/10.1016/j.wasman.2020.03.039

[6] Zhang, J., Jia, C.R., Xia, X.F. (2013). Base on set pair analysis for rural domestic refuse treatment technology evaluation. In Advanced Materials Research, 781-784: 2013–2016. http://dx.doi.org/10.4028/www.scientific.net/AMR.781-784.2013

[7] Zhou, Q.S. (2018). Demand and Supply of Agricultural Organic Waste Composting. Beijing: Science Press, ISBN: 978-7-03-025910-3.

[8] Wu, D., Zhang, C., Lü, F., Shao, L., He, P. (2014). The operation of cost-effective on-site process for the bio-treatment of mixed municipal solid waste in rural areas. Waste Management, 34(6): 999-1005. http://dx.doi.org/10.1016/j.wasman.2013.12.002

[9] Huang, K., Wang, J., Bai, J., Qiu, H. (2013). Domestic solid waste discharge and its determinants in rural China. China Agricultural Economic Review, 5(4): 512-525. http://dx.doi.org/10.1108/CAER-02-2012-0008

[10] Yang, T., Li, Y., Gao, J., Huang, C., Chen, B., Zhang, L., Wang, X., Zhao, Y., Xi, B., Li, X. (2015). Performance of dry anaerobic technology in the co-digestion of rural organic solid wastes in China. Energy, 93: 2497-2502. http://dx.doi.org/10.1016/j.energy.2015.10.014

[11] Mia, S., Uddin, M.E., Kader, M.A., Ahsan, A., Mannan, M.A., Hossain, M.M., Solaiman, Z.M. (2018). Pyrolysis and co-composting of municipal organic waste in Bangladesh: A quantitative estimate of recyclable nutrients, greenhouse gas emissions, and economic benefits. Waste Management, 75: 503-513. https://doi.org/10.1016/j.wasman.2018.01.038

[12] Jamroz, E., Bekier, J., Medynska-Juraszek, A., Kaluza-Haladyn, A., Cwielag-Piasecka, I., Bednik, M. (2020). The contribution of water extractable forms of plant nutrients to evaluate MSW compost maturity: A case study. Scientific Reports, 10(1): 1-9. http://dx.doi.org/10.1038/s41598-020-69860-9

[13] Cestonaro, T., de Vasconcelos Barros, R.T., de Matos, A.T., Costa, M.A. (2020). Full scale composting of food waste and tree pruning: How large is the variation on the compost nutrients over time? Science of The Total Environment, 754: 142078. http://dx.doi.org/10.1016/j.scitotenv.2020.142078

[14] Radziemska, M., Vaverková, M.D., Mazur, Z. (2019). Pilot scale use of compost combined with sorbents to phytostabilize Ni-contaminated soil using lolium perenne L. Waste and Biomass Valorization, 10(6): 1585-1595. http://dx.doi.org/10.1007/s12649-017-0166-9

[15] Cao, Y., Wang, X., Bai, Z., Chadwick, D., Misselbrook, T., Sommer, S.G., Qin, W., Ma, L. (2019). Mitigation of ammonia, nitrous oxide and methane emissions during solid waste composting with different additives: A meta-analysis. Journal of Cleaner Production, 235: 626-635. https://doi.org/10.1016/j.jclepro.2019.06.288

[16] Yu, K., Li, S., Sun, X., Kang, Y. (2020). Maintaining the ratio of hydrosoluble carbon and hydrosoluble nitrogen within the optimal range to accelerate green waste composting. Waste Management, 105: 405-413. https://doi.org/10.1016/j.wasman.2020.02.023

[17] Surendra, K.C., Takara, D., Hashimoto, A.G., Khanal, S.K. (2014). Biogas as a sustainable energy source for developing countries: Opportunities and challenges. Renewable and Sustainable Energy Reviews, 31: 846-859. http://dx.doi.org/10.1016/j.rser.2013.12.015

[18] Li, Y., Jin, Y., Li, J., Nie, Y. (2016). Enhanced nitrogen distribution and biomethanation of kitchen waste by thermal pre-treatment. Renewable Energy, 89: 380-388. https://doi.org/10.1016/j.renene.2015.12.029

[19] Aleluia, J., Ferrão, P. (2017). Assessing the costs of municipal solid waste treatment technologies in developing Asian countries. Waste Management, 69: 592-608. https://doi.org/10.1016/j.wasman.2017.08.047

[20] Zhao, Y., Zhou, Q., Hidetoshi, K., Luo, L. (2021). Nitrogen flow characteristics of solid waste in China. Ecotoxicology and Environmental Safety, 208: 111596. https://doi.org/10.1016/j.ecoenv.2020.111596

[21] Bernardes, C., Günther, W.M.R. (2014). Generation of domestic solid waste in rural areas: case study of remote communities in the Brazilian Amazon. Human Ecology, 42(4): 617-623. http://dx.doi.org/10.1007/s10745-014-9679-z

[22] Zhou, Q.S. (2018). Efficient Wide Area Utilization of Agricultural Organic Waste Composting. Beijing: China Agricultural Press, ISBN: 978-7-109-24631-7.

[23] Liu, L.L., Zhang, Z.X. (2017). Comprehensive Utilization Technology of Straw. Beijing: Chemical Industry Press.

[24] Zhao, T.T., Mei, J., Zhao, Y.C. (2017). Principle and Technology of Solid Waste Composting. Chemical Industry Press, ISBN: 978-7-122-28023-7.

[25] Cui, S., Shi, Y., Groffman, P.M., Schlesinger, W.H., Zhu, Y.G. (2013). Centennial-scale analysis of the creation and fate of reactive nitrogen in China (1910–2010). Proceedings of the National Academy of Sciences, 110(6): 2052-2057. https://doi.org/10.1073/pnas.1221638110

[26] Luo, Z., Lam, S.K., Hu, S., Chen, D. (2020). From generation to treatment: A systematic reactive nitrogen flow assessment of solid waste in China. Journal of Cleaner Production, 259: 121127. https://doi.org/10.1016/j.jclepro.2020.121127

[27] NBS Henan Survey Team. (2018). Henan Statistical Yearbook. Beijing: China Statistics Press.

[28] Aramaki, T., Suzuki, E., Hanaki, K. (2001). Supply and demand analysis of compost for effective use of various organic wastes in Aichi Prefecture. Journal of Environmental Science (Japan), 14(4): 367-371.

[29] Zhou, Q.S., Wang, Y., Han, T., Li, Y.L., Zhang, Y.C. (2017). The demand & supply balance analysis for organic matter of the agricultural waste in Yongcheng City. Chemical Engineering Transactions, 62: 1321-1326. https://doi.org/10.3303/CET1762221