Spatial Distribution and Pollution Source Analysis of Heavy Metals in Cultivated Soil in Ningxia

Abstract

This study collected 820 topsoil samples from cultivated lands across Ningxia, covering the Yellow River irrigation area, the central arid zone, and the southern mountainous region. The ordinary kriging were spatially interpolated to analyze As, Hg, Cd, Cr, and Pb heavy-metal pollution spatial patterns. Pollution was evaluated using the Nemerow and geoaccumulation (I_(geo)) indices, and sources quantified via Pearson correlations, PCA (Principal Component Analysis), and PMF (Positive Matrix Factorization). The results indicated that Hg and Cd posed the highest ecological risks. The overall mean concentrations (mg.kg⁻¹) of Hg, Cd, As, Pb, and Cr were 0.04, 0.27, 9.91,23.81, and 57.34, respectively. Compared with the background values, they were 1.90, 2.41, 0.83, 1.14, 2.74 times higher, respectively. Geospatially, regions with higher pollution probabilities for Cd, Cr, Pb, Hg, and As were concentrated in the northern and central parts of Ningxia, whereas the southern region exhibited lower pollution probabilities. pH significantly influenced the accumulation and spatial distribution of heavy metals in soil. Source apportionment identified three primary contributors: transportation and natural parent materials (As, Pb, Cr), industrial activities (Hg), and agricultural practices (Cd). Hg and Cd were identified as the key risk elements requiring prioritized management. These results enhance understanding of the pollution levers of heavy metals in Ningxia cultivated soils, and also provide foundation for developing more scientific and precise soil risk control policies, offering significant practical value for environmental risk management.

1. Introduction

High-quality and sustainable agricultural development in China hinges on well-cultivated soil, which directly impacts agricultural product quality, safety, food security, and human health [1]. The initial nationwide soil pollution survey in 2014 revealed that 16.1% of farmland soil in China exceeded standards, with varying degrees of pollution: slight (11.2%), mild (2.3%), moderate (1.5%), and severe (1.1%) [2]. The main pollutants contributing to this were Cd, Hg, As, Cu, Pb, Cr, Zn, and Ni, accounting for 82.4%. Factors such as population growth, urbanization, industrialization, climate change, smelting and pesticide use may accelerate the accumulation of heavy metals in soil [3], which persist for extended periods and are absorbed by plant roots, entering the food chain and posing risks to organisms within it [4]. The accumulation of heavy metals in soil is influenced by regional environmental changes and human activities, leading to complex and unpredictable spatial distributions [5]. Heavy metal pollution in cultivated soil significantly jeopardizes agricultural product safety, with long-lasting and costly consequences once soil is contaminated [6,7]. Therefore, It is critical to proactively address and mitigate sources of heavy-metal pollution in cultivated soils to safeguard soil and agricultural-product quality, while also identifying currently unpolluted regions that are vulnerable to future contamination [8].

In recent years, various techniques and models have been employed to assess the origins of heavy metal contamination in agricultural soils. These methods can be broadly categorized into qualitative identification of pollution sources and quantitative analysis of pollution sources [9]. Qualitative identification primarily involves determining the primary pollution sources through multivariate statistical analysis and principal component analysis. On the other hand, quantitative analysis utilizes receptor models, such as positive matrix factorization (PMF), chemical mass balance (CMB), and Unmix model [10,11], to quantify the sources of contamination. Among these analytical tools, PMF analysis is commonly utilized due to its constraint of non-negative values in the factor matrix, enabling the derivation of more practical factors [12]. Initially utilized for source apportionment of atmospheric particles, PMF analysis has been increasingly applied to analyze heavy metal sources in water, soil, and sediment [13,14]. The outcomes demonstrated the model is efficacy in identifying pollution sources and determining their respective contributions to heavy metal concentrations. Consequently, the PMF model has been employed for evaluating heavy metal levels in cultivated soils.

Ningxia, located in Northwest China, represents an arid/semi-arid, irrigated agro-ecosystem with legacy coal-chemical/metallurgical activities and Yellow River irrigation. Moreover, the environmental sensibility and fragility of the area also make it of great significance. The soil quality of farmland in Ningxia is under threat from various heavy metal pollutants due to rapid urbanization and the continuous progress of modern industry and agriculture. However, prior studies seldom integrate PMF with ordinary kriging to produce spatially explicit and source-attributed risk maps for cultivated soils. Therefore, there is an urgent need to investigate heavy metal pollution of typical farmland in the Ningxia Hui Autonomous Region. This study aims to analyze the spatial distribution trends of farmland soil heavy metals As, Hg, Cd, Cr, and Pb and evaluate their associated ecological risks. It also seeks to predict and provide early warnings for the environmental quality of heavy metals across different future periods and propose corresponding prevention measures. The findings of this study are valuable for elucidating the long-term fate of cultivated soil heavy metals and offer a theoretical foundation for soil pollution prevention and management for other similar areas.

2. Materials and Methods

2.1. Overview of the Study Area

The Ningxia Hui Autonomous Region is located in Northwestern China, bordered by Shaanxi Province to the east, Inner Mongolia Autonomous Region to the west and north, and Gansu Province to the south, spanning between 35°14′ to 39°23′ N and 104°17′ to 107°39′ E. The region has a narrow north-south terrain, with elevations higher in the south that gradually decrease toward the north, characterized by significant elevation differences in the west and gentle undulations in the east. Benefiting from irrigation by the Yellow River, Ningxia is renowned as the “frontier south of the Yangtze River, the land of fish and rice.” The cultivated land area in Ningxia spans about 1.3 million hectares, with annual precipitation ranging from 167.2 mm to 618.3 mm, decreasing from south to north and occurring mainly in summer months.

2.2. Sample Collection and Analysis

Soil samples were collected between June and August 2024 from key cultivated areas across the region, taking into account soil type, land use, cultivated area, and farming practices. Following a preliminary assessment of the farmland soil environment, areas with significant heavy-metal pollution were identified for targeted sampling. A combination of random and grid sampling was employed across Ningxia, and GPS was used to record the precise coordinates of each soil sample. In total, 820 soil samples were collected (Figure 1). At each site, five subsamples were taken at 0–20 cm from the four corners and the center of a 10 m × 10 m square using a wooden shovel and were composited. Approximately 1 kg of the composite was retained using the quartering method, properly labeled, bagged, and recorded in a dedicated data-collection application. The collected soil samples were air-dried, debris such as stones and plant roots was removed, then samples were sieved through a 2-mm mesh; a portion was further ground to pass a 0.15-mm sieve before final storage.

All soil samples naturally air-dried and avoid direct sunlight, removing animal and plant residues, stones and plant roots. The passed soil sample was ground until it passed through a 0.149 mm sieves, and finally stored for future use. The soil samples were digested using the microwave digestion method of HCl, HNO3, HF, H₂O₂. The Pb, Cd, Cr, Hg and As were determined by inductively coupled plasma mass spectrometry (ICP-MS, NexION300X, PE, PerkinElmer, Waltham, MA, USA). Each batch of sample analysis was set to 3 replicates, and the national standard soil samples (GSS-4 and GSS-6) were used for quality control and assurance. Soil salinity was measured using the conductivity method, and soil cation exchange capacity (CEC) was determined using the resin method. The relative deviation of the measurement was controlled within ±10%. The pH value of the soil sample is determined by the potentiometric method (water-soil ratio is 2.5:1).

2.3. Data Processing

The soil samples were analyzed for heavy metal content using SPSS 21.0 for descriptive and qualitative analyses, EPA PMF 5.0 for quantitative analysis of heavy metals in cultivated soil, and ArcGIS 10.7 for assessing the spatial distribution characteristics of heavy metals in the cultivated soil.

2.4. Research Technique

2.4.1. Nemero Integrated Pollution Index Method

The Nemerow Integrated Pollution Index, introduced by the American researcher Nemerow, offers a comprehensive assessment of the pollution levels of various factors by considering both extreme and average values. This index effectively evaluates the overall pollution status of heavy metals at individual sampling points within the research area. Widely utilized, it stands as a prominent method for the holistic appraisal of pollution within a study area. The calculation formula is as follows:

$$\mathrm{Pi} = {\displaystyle \raisebox{1ex}{$\mathit{Ci}$}\!\left/ \!\raisebox{-1ex}{$\mathit{Si}$}\right.}$$

$$P_N =\sqrt{{\displaystyle \raisebox{1ex}{$(P_{\mathit{imax}}^2+P_{\mathit{iave}}^2)$}\!\left/ \!\raisebox{-1ex}{$2$}\right.}}$$

In this study, P_i represents the pollution index of pollutant i in the soil, C_i denotes the measured content of pollutant i, and S_i stands for the evaluation reference value of pollutant i. P_N signifies the Nemerow comprehensive pollution index, P_imax is the maximum value of the single pollution index of heavy metal pollutant i at the sampling point, and P_iave represents the average value of the single pollution index of heavy metal pollutants at the sampling point.

The evaluation standard utilized for risk screening was the Soil Environmental Quality Agricultural Land Soil Pollution Risk Control Standard (GB15618-2018). Appendix A 

Table A1. Classification standard of Nemero index evaluation method.

Classification	Pi	PN	Pollution Level
I	P	P	Safe
II	0.7 < P	0.7 < P	Low
III	1.0 < P	1.0 < P	Moderate
IV	2.0 < P	2.0 < P	High
V	Pi > 3.0	P	Very high

and

Table A2. Classification and hazard class of heavy metal potential ecological hazard index.

${\mathbf{E}}_{\mathbf{r}}^{\mathbf{i}}$	RI	Classification of Potential Ecological Risk Factor
≦40	RI ≦ 150	Low
40 < $E_r^i$ ≦ 80	150 < RI ≦ 300	Moderate
80 < $E_r^i$ ≦ 160	300 < RI ≦ 600	Considerable
160 < $E_r^i$ ≦ 320	600 < RI ≦ 1200	High
>320	RI > 1200	Very high

display the classification criteria for the single-factor pollution index and Nemerow index evaluation method.

2.4.2. Potential Ecological Risk Index Method

The Potential Ecological Risk Index method was introduced by the Swedish researcher Hakanson. This approach assesses the potential ecological risk posed by heavy metals in soil while accounting for their ecological toxicity [15]. The calculation formula for this method is as follows.

$$\mathrm{RI}={\sum }_{i=1}^n{E}_{r }^i={\sum }_{i=1}^n(T_r^i\times C_f^i)={(T}_r^i\times {\displaystyle \frac{c_i}{c_n^i}})$$

where, RI represents the integrated potential ecological hazard index of heavy metals, C_i denotes the concentration of heavy metal i, ${\mathrm{c}}_{\mathrm{n}}^{\mathrm{i}}$ stands for the background concentration of heavy metal i (mg/kg) specific to Ningxia soil, ${\mathrm{C}}_{\mathrm{f}}^{\mathrm{i}}$ signifies the pollution index of heavy metal i in soil, ${\mathrm{T}}_{\mathrm{r}}^{\mathrm{i}}$ represents the biological toxicity response factor of heavy metal i, and ${\mathrm{E}}_{\mathrm{r}}^{\mathrm{i}}$ indicates the potential ecological hazard index of heavy metal i in soil.

The biological toxicity coefficients for Cd, Cr, Pb, Hg, and As are 30, 2, 5, 40, and 10, respectively. The number of different risk, ${\mathrm{E}}_{\mathrm{r}}^{\mathrm{i}}$ and RI values are listed in Table 1 and Table 2.

2.4.3. Geoaccumulation Index Method

The geoaccumulation index method is a crucial parameter for discerning the influence of human activities, as outlined by previous studies [16,17]. The calculation formula is presented below:

$$I_{\mathit{geo}} ={\log }_2(C_i/1.5B_i)$$

The geoaccumulation index (I_(geo)) represents the concentration of heavy metal(C_i) in comparison to its background value (B_i), which is determined using the background value of heavy metal i in Ningxia soil and a correction factor of 1.5. The pollution levels are classified into seven grades based on the geoaccumulation index I_(geo) ≤ 0 indicates no pollution;0 < I_(geo) ≤ 1 signifies light pollution; 1 < I_(geo) ≤ 2 indicates moderate-leaning pollution; 2 < I_(geo) ≤ 3 indicates moderate pollution; 3 < I_(geo) ≤ 4 signifies heavy-leaning pollution; 4 < I_(geo) ≤ 5 indicates heavy pollution; and values exceeding 5 represents severe pollution.

2.4.4. Indicator Kriging

Journel proposed Indicator Kriging, a widely utilized method in soil pollution studies due to its ability to address extreme values and high deviation characteristics [18]. This study applied ordinary kriging to interpolate the spatial distribution of soil heavy metals. The reliability of the interpolation was evaluated through semivariogram model fitting and leave-one-out cross-validation (LOOCV). First, empirical semivariograms for each heavy metal were computed from the sampling data and fitted with a spherical model. The predictive performance of the interpolation model was assessed using LOOCV. he final spatial distribution maps were produced in ArcGIS 10.2 with standardized legends, scale bars, and north arrows.

2.4.5. Principal Component Analysis

Principal component analysis-multiple linear regression (PCA-MLR) was employed to discern pollution sources in the research area. Following the determination of pollution factor quantities, a multiple linear regression analysis was conducted on the concentration of individual tracer elements. This process yielded regression equations linking the concentration of heavy metals to each tracer element’s concentration. The regression coefficients were utilized to compute the relative contribution of each pollution source.

2.4.6. PMF Model

Positive matrix factorization (PMF) is a data analysis technique rooted in factor analysis principles. The PMF model decomposes the initial matrix X_(i×j) into two factor matrices, F_(k×j) and G_(i×k), along with a residual matrix E_(i×j), according to the following equation:

$$X_{\mathit{ij}} = {\sum }_{k=1}^p{G}_{\mathit{ik}}{F}_{\mathit{kj}}+ E_{\mathit{ij}}$$

Let X_ij represents the concentration of the jth chemical component in the ith sample, G_ik denotes the contribution of the ith sample in source k (contribution rate matrix of the source), F_kj indicates the concentration of the jth chemical component in source k (source component spectrum matrix), and E_ij stands for the residual matrix.

PMF defines the objective function Q as follows:

$$\mathrm{Q}={\sum }_{\mathrm{i}=1}^{\mathrm{n}}{\sum }_{\mathrm{j}=1}^{\mathrm{m}}\left({\displaystyle \frac{{\mathrm{E}}_{\mathrm{ij}}}{{\mathrm{U}}_{\mathrm{ij}}}}\right)$$

where U_ij represents the uncertainty of the jth chemical component in the ith sample.

The PMF software necessitates the submission of concentration and uncertainty files. The uncertainty data files were computed in the following manner:

$$\mathrm{Unc}=5/6\times \mathrm{MDL}$$

The uncertainty value is determined when the concentration of each element exceeds its respective method detection limit (MDL).

$$\mathrm{Unc}=\sqrt{{(\mathsf{\alpha } \times \mathrm{c})}^2+{(0.5 \times \mathrm{MDL})}^2}$$

The relative standard deviation (RSD) is defined as the ratio of the standard deviation to the mean of a dataset, where the standard deviation represents the variability within the data. The elemental concentration refers to the amount of a specific element present in a sample, while the method detection limit (MDL) signifies the lowest concentration of an analyte that can be reliably detected by a given method.

The signal-to-noise ratio (SNR) serves as the primary diagnostic tool in the model, distinguishing genuine variability in measured values from data interference. A lower SNR indicates greater instability in the chemical composition within the model, reducing the likelihood of sample detection. The determination of the number of Positive Matrix Factorization (PMF) factors is based on the analysis of multiple experiments, errors, and relative changes in the Q values [19,20].

3. Results

3.1. Statistical Analysis of Heavy Metal Content

Table 1 presents the key statistical parameters of five heavy metals within the study area. The levels of risk were determined based on the screening and risk control values outlined in the Soil Environmental Quality Control Standard for Soil Pollution of Agricultural Land (referred to as GB15618-2018). Soil contamination in agricultural land is classified as low risk when heavy metal concentrations are at or below the risk screening value, typically considered negligible. Conversely, if heavy metal levels exceed the risk screening value but are equal to or below the risk control value, there is a medium risk of soil pollution, potentially impacting the quality and safety standards of edible agricultural products. In such cases, mitigation measures like agronomic adjustments and crop diversification are recommended [21,22]. When heavy metal concentrations surpass the risk control value, indicating a high risk of soil pollution leading to non-compliance of edible agricultural products with safety standards, conventional mitigation strategies may be insufficient. Under these circumstances, stringent measures such as banning the cultivation of edible crops and converting farmland to forested areas are advised [23].

The study indicated low levels of heavy metal pollution in the agricultural soil, with 816 areas classified as low risk for Cd, while Cr, Pb, Hg, and As were all deemed low risk (Table 1). None of the average heavy metal contents exceeded the risk screening values outlined in GB15618-2018. The coefficient of variation (CV) was utilized to assess the dispersion of heavy metal content, with a CV exceeding 0.36 indicating high variation. The variation degree of heavy metals in Table 1 ranked as Hg > Cd > Cr > As > Pb, with Hg exhibiting the highest variation (CV > 0.36), suggesting significant susceptibility to external influences and human activities. Overall, the ecological risk to cultivated soil in the study area was low, with Cd and Hg posing pollution risks.

Table 1. Characteristics of heavy metal content in surface soil of the study area.

Item	Number	Number of Different Risk b Points			Background c Values (mg/kg)	MDL (mg/kg)	Max (mg/kg)	Min (mg/kg)	Mean (mg/kg)	CV
		Low	Medium	High
Cd	820	816	2	2	0.112	0.03	0.61	0.1	0.27	0.3
Cr	820	820	0	0	60	1.0	97.2	14.3	57.34	0.28
Pb	820	820	0	0	20.9	2.1	52.4	10.4	23.81	0.19
Hg	820	820	0	0	0.021	0.002	0.18	0.003	0.04	0.47
As	820	820	0	0	11.9	0.01	20.3	1.77	9.91	0.24
PH	820	— a	—	—	—	—	9.09	6.45	8.18	0.04
OM (g/kg)	820	—	—	—	—	—	61.5	2.31	14.35	0.43
CEC (cmol/kg)	820	—	—	—	—	—	18.3	3.1	10.95	0.2

Note: ^a “—” indicates that relevant data are not monitored; ^b Soil environmental quality risk control standard for soil contamination of agricultural land (GB15618-2018); ^c National Environmental Protection Agency of China (NEPA) & China National Environmental Monitoring Center (CNEMC). (1990) [20].

Table 1. Characteristics of heavy metal content in surface soil of the study area.

Item	Number	Number of Different Risk b Points			Background c Values (mg/kg)	MDL (mg/kg)	Max (mg/kg)	Min (mg/kg)	Mean (mg/kg)	CV
		Low	Medium	High
Cd	820	816	2	2	0.112	0.03	0.61	0.1	0.27	0.3
Cr	820	820	0	0	60	1.0	97.2	14.3	57.34	0.28
Pb	820	820	0	0	20.9	2.1	52.4	10.4	23.81	0.19
Hg	820	820	0	0	0.021	0.002	0.18	0.003	0.04	0.47
As	820	820	0	0	11.9	0.01	20.3	1.77	9.91	0.24
PH	820	— a	—	—	—	—	9.09	6.45	8.18	0.04
OM (g/kg)	820	—	—	—	—	—	61.5	2.31	14.35	0.43
CEC (cmol/kg)	820	—	—	—	—	—	18.3	3.1	10.95	0.2

Note: ^a “—” indicates that relevant data are not monitored; ^b Soil environmental quality risk control standard for soil contamination of agricultural land (GB15618-2018); ^c National Environmental Protection Agency of China (NEPA) & China National Environmental Monitoring Center (CNEMC). (1990) [20].

3.2. Heavy Metal Pollution Assessment and Risk Assessment of Cultivated Soil

3.2.1. Evaluation of Soil Comprehensive Pollution Index

The pollution levels of heavy metals at various sampling points were assessed based on P_i, P_N, and RI criteria. Ecological risk assessment of heavy metal pollution in cultivated soil in Ningxia was conducted using single-factor pollution index and Nemerow comprehensive pollution index [24]. Analysis presented in Table 2 revealed that the levels of Cr, Pb, and Hg were within safe limits, while Cd and As were at warning levels in 3.17% and 0.37% of the sample points, respectively. Additionally, Cd was found to be at a light pollution level in 0.27% of the sample points. Applying the Nemerow comprehensive pollution index to evaluate heavy metal contamination in soil, it was determined that 0.49% of the soil samples in the study area fell within the warning range. Furthermore, the Nemerow comprehensive pollution index for other heavy metal samples in the cultivated soil was below 0.7, indicating a safe pollution level.

Based on the potential ecological risk index (${\mathrm{E}}_{\mathrm{r}}^{\mathrm{i}}$) classification for heavy metal content in soil, the distribution of ecological risk levels was as follows: 0.12% of Hg samples exhibited extremely strong ecological risk, 1.10% showed very strong ecological risk, 38.05% indicated relatively strong ecological risk. Specifically, Cd elements were present in 0.49% of samples with strong ecological risk, 30.12% with moderate ecological risk, 66.83% with medium ecological risk; other heavy metal elements posed only slight ecological risks. In terms of the comprehensive ecological risk index (RI) for soil heavy metals, among the 820 sampling points within the study area, 0.12% were classified as having strong ecological risk, 60% as medium ecological risk, no sampling points with strong or extremely strong ecological risk.

Table 2. Presents the statistics concerning heavy metal pollution index and potential ecological risk index within the research area.

Item	Pollution Index	Proportion of Sampling Points at Different Pollution Levels (%)					Ecological Hazard Index a	Proportion of Sampling Sites with Different Ecological Risk Levels (%)
		Safe	Alert	Mild	Moderate	Severe		Mild	Moderate	Strong	Very Strong	Extremely Strong
Cd	Pi	96.56	3.17	0.27	0	0	$E_r^i$	2.56	66.83	30.12	0.49	0
Cr	Pi	100	0	0	0	0	$E_r^i$	100	0	0	0	0
Pb	Pi	100	0	0	0	0	$E_r^i$	100	0	0	0	0
Hg	Pi	100	0	0	0	0	$E_r^i$	19.39	41.34	38.05	1.10	0.12
As	Pi	99.63	0.37	0	0	0	$E_r^i$	100	0	0	0	0
PN		99.51	0.49	0	0	0	RI	39.88	60	0.12	0	0

Note: ^a Hakanson, L. (1980) [19]. An ecological risk index for aquatic pollution control.

Table 2. Presents the statistics concerning heavy metal pollution index and potential ecological risk index within the research area.

Item	Pollution Index	Proportion of Sampling Points at Different Pollution Levels (%)					Ecological Hazard Index a	Proportion of Sampling Sites with Different Ecological Risk Levels (%)
		Safe	Alert	Mild	Moderate	Severe		Mild	Moderate	Strong	Very Strong	Extremely Strong
Cd	Pi	96.56	3.17	0.27	0	0	$E_r^i$	2.56	66.83	30.12	0.49	0
Cr	Pi	100	0	0	0	0	$E_r^i$	100	0	0	0	0
Pb	Pi	100	0	0	0	0	$E_r^i$	100	0	0	0	0
Hg	Pi	100	0	0	0	0	$E_r^i$	19.39	41.34	38.05	1.10	0.12
As	Pi	99.63	0.37	0	0	0	$E_r^i$	100	0	0	0	0
PN		99.51	0.49	0	0	0	RI	39.88	60	0.12	0	0

Note: ^a Hakanson, L. (1980) [19]. An ecological risk index for aquatic pollution control.

3.2.2. Evaluation of Geoaccumulation Index

The accumulation index of heavy metal elements in cultivated soil within the study area was determined using the Ningxia soil background values [20]. The results indicate that the heavy metal pollution levels in cultivated soil in Ningxia are predominantly low (see

Table 3. Presents the geoaccumulation index (I_(geo)) ^a for heavy metal accumulation in cultivated soil in Ningxia (mg/kg).

Item	Max	Min	Proportion of Sample Points by Different Pollution Levels a (%)
			No Pollution	Mild	Moderate-Tending	Moderate	Severe-Tending	Severe	Critical
Cd	0.61	0.10	7.93	74.39	17.70	0	0	0	0
Cr	97.20	14.30	99.76	0.24	0	0	0	0	0
Pb	52.40	10.40	96.70	3.30	0	0	0	0	0
Hg	0.18	0.003	29.76	61.34	8.78	0	0	0	0
As	20.30	1.77	99.63	0.37	0	0	0	0	0

Note: ^a Soil environmental quality risk control standard for soil contamination of agricultural land (GB15618-2018).

), with the exception of Cd and Hg. For Cd, 74.39% as lightly polluted, and 17.70% as moderately polluted. Regarding Hg, 61.34% were lightly polluted, and 8.78% were moderately polluted. Furthermore, Cr, Pb, and As exhibited non-pollution levels in 99.76%, 96.70%, and 99.63% of the samples, respectively, while light pollution levels were observed in 0.24%, 3.30%, and 0.37% of the samples, respectively.

3.3. Analysis of Spatial Distribution Characteristics of Heavy Metals and pH

Geostatistical analysis of five heavy metals in Ningxia cultivated soil was conducted using ArcGIS 10.2 software, employing the Kriging interpolation method to map their spatial distribution [25] (Figure 2). The spatial patterns of As and Cr exhibit similarities, with elevated concentrations observed in the northern, northwestern, and central regions of Ningxia, while lower levels are found in the eastern and southern areas. High concentrations of Hg are concentrated in the northern and eastern parts of Ningxia, with additional elevated areas in the southern region, whereas lower levels are present in the central and western areas. Cd concentrations are pre-dominantly elevated in the central and eastern regions, with additional high-value areas in the north, west, and south. Pb concentrations peak in the northern and central regions of Ningxia.

Overall, Figure 3 shows the experimental semivariogram and the fitted spherical model for soil heavy metals. The theoretical model demonstrates a good fit to the experimental data, effectively. All heavy metals exhibit elevated concentrations in the central and northern regions, with widespread high values observed for Hg and Cd. The heavy metal content is lower in the high-pH regions of cultivated soils.

3.4. Analysis of Heavy Metal Sources

3.4.1. Correlation Analysis of Heavy Metals in Soil

Pearson correlation analysis revealed significant negative correlations between soil pH and soil organic matter, cation exchange capacity, As, Hg, Cd, and Cr. Additionally, soil pH exhibited negative correlations with As and Cr. Soil organic matter showed positive correlations with cation exchange capacity, As, Hg, Pb, and Cr. Conversely, soil salt content displayed negative correlations with cation exchange capacity, As, Hg, Pb, and Cr. Furthermore, As exhibited significant positive correlations with Pb and Cr, suggesting strong homology among these elements. Notably, Hg demonstrated an extremely significant positive correlation with Cr, indicating potential similarities in their migration patterns or sources (Figure 4).

3.4.2. Principal Component Analysis of Heavy Metals in Soil

Principal component analysis (PCA) was employed to investigate the sources of heavy metals in cultivated soil in Ningxia. The Kaiser-Meyer-Olkin (KMO) value for the distribution of five heavy metals was 0.636, surpassing the significance threshold of 0.01, affirming the suitability of PCA for elucidating the correlation among heavy metal sources in Ningxia soil. Prior to PCA, data underwent averaging to account for variations in the magnitude of heavy metals. Through assessment of eigenvalues, cumulative explained variances, and factor loadings, three principal components were derived (see

Table 4. Principal Component Matrix of Heavy Metals in Cultivated Soil.

Item	PC1	PC2	PC3
As	0.81	−0.061	−0.092
Cr	0.694	0.13	0.401
Cd	−0.184	0.844	0.05
Pb	0.41	0.646	−0.047
Hg	0.038	−0.007	0.955
Eigenvalue	1.529	1.084	0.964
Variance Contribution Rate (%)	30.57	21.67	19.28
Cumulative Variance Contribution Rate	30.57	52.24	71.52

), collectively elucidating 71.52% of the variance. Specifically, the first principal component (PC₁) explained 30.57% of the variance, followed by the second (PC₂) at 21.67% and the third (PC₃) at 19.28%. PC₁ exhibited higher positive loadings for As and Cr, suggesting a common source for these heavy metals in agricultural soils. Cd displayed elevated positive loadings in PC₂, while Hg exhibited the same in PC₃.

3.4.3. PMF Heavy Metal Quantitative Source Analysis

The PMF model was employed to assess the origins of heavy metals in cultivated soil in Ningxia [26]. Experimental data were inputted into the EPA PMF 5.0 software. Pollution factors with a signal-to-noise ratio exceeding 1 were considered “strong” variables. The model was configured to include 3 to 7 factors, model was iterated at least 100 times. The optimal number of factors was determined by comparing Qrob/Qexp values, where Qrob represents the optimal solution of the objective function Q obtained in Robust mode, and Qexp represents the true value of objective function Q. The model performed best with three factors, as indicated by minimal discrepancies between Qrobust and Qtrue, standard residuals of each element falling within the range of −3 to 3, and optimal fit. The fitting results of the measured values and the predicted values of the model are shown in Figure 5. The determination coefficients of all heavy metals were higher than 0.6, indicating that the PMF model has a good fitting effect. Therefore, the model meets the research needs, and the number of factors can fully explain the information contained in the original data. These findings are summarized in

Table 5. Presents the fitting results comparing measured values with simulated predicted values of soil heavy metal content.

Item	R2	Slope	Intercept
Pb	0.647	0.408	13.07
As	0.676	0.46	4.795
Cd	0.841	0.747	0.06
Cr	0.784	0.8	9.627
Hg	0.998	0.998	0.001

, demonstrating that the selected number of factors in the PMF model effectively captures the information within the original dataset.

The analysis of Figure 6 and Figure 7 reveals that factor 1 significantly contributes to As, Pb, and Cr at rates of 62.5%, 46.1%, and 76.2%, respectively. These elements exhibit a strong correlation at a significance level of 1%, suggesting a common pollution source. Previous research has identified natural and anthropogenic sources of As in soil, with As-containing oxides and sulfide rocks migrating to cultivated soil layers through weathering and erosion processes [27,28]. The average As content in cultivated land in Ningxia (9.91 mg/kg) is notably lower than the regional soil’s background value for heavy metals (11.9 mg/kg), indicating a potential contribution from natural parent materials. Pb serves as a key indicator of traffic-related emissions, particularly from vehicular combustion [29]. Given the proximity of a substantial portion of cultivated land to roadways, Pb contamination in cultivated soil is plausible. Conversely, Cr is commonly associated with soil parent material composition and is typically considered a low-level pollutant [30]. Analysis in Table 3 and Table 4 indicates that the ecological risk index for Cr suggests a minor risk level, with 99.76% of samples exhibiting non-polluted levels based on the geoaccumulation index. Consequently, factor 1 is inferred to originate from a combination of transportation-related sources and natural parent materials.

Factor 2 significantly contributes to the presence of mercury (Hg) at a rate of 85.7%. An evaluation of potential ecological risk indicates that 38.05% of the sampled sites exhibit Hg pollution, with Hg displaying the highest coefficient of variation in the research area, suggesting substantial impact from human activities on cultivated soil. Previous research has established a correlation between Hg contamination and coal combustion [31]. The northern region of the study area is characterized by a thriving energy sector. Emissions from processing facilities, including airborne chromium compounds, lead to varying degrees of heavy metal contamination in the surrounding soil through dry and wet deposition of industrial emissions [32,33]. This contaminated soil is a primary source of pollution for crops, particularly vegetables. Field investigations and sampling in the study area have uncovered instances of unauthorized discharge of untreated or substandard industrial wastewater into agricultural channels via concealed pipelines [34]. Consequently, farmers irrigate their fields with polluted water, resulting in Hg accumulation in the soil. Furthermore, there are instances of haphazardly disposed industrial waste materials (e.g., smelting by-products and electroplating residues) near some sampled cultivated areas, facilitating Hg infiltration into the soil through runoff. Hence, Factor 2 is identified as an industrial contamination source.

Factor 3 accounted for 72.1% of the cadmium (Cd) content. The average Cd levels exceed the background levels in Ningxia soil, indicating potential influence from human activities. Previous research suggests that agricultural practices can result in Cd accumulation in soil [35,36,37,38]. The Yinchuan Plain, a significant grain-producing region in northwest China with a long history of agricultural development, exhibits substantial fertilizer usage, suggesting a plausible link between Cd levels and agricultural activities in the area. Cd, a prominent component of pesticides and fertilizers, is prone to migration and volatilization. Prolonged use of these substances can lead to Cd buildup in the soil [38]. Furthermore, certain agricultural inputs, such as livestock manure, may also contain Cd, possibly originating from feed additives [39,40]. Excessive application of chemical fertilizers, pesticides, and organic fertilizers poses a significant risk of Cd pollution in cultivated lands [41]. Data from the Ningxia Statistical Yearbook indicates an annual application of approximately 900,000 tons of chemical fertilizers in cultivated soil, which can result in cumulative effects over time. Therefore, Factor 3 is identified as originating from agricultural production activities.

In summary, the apportionment of the three source factors to the presence of the five heavy metals is as follows: Arsenic (As), Lead (Pb), and Chromium (Cr) predominantly originated from a combination of transportation sources and natural parent materials, Mercury (Hg) primarily stemmed from industrial activities, and Cadmium (Cd) chiefly emanated from agricultural practices.

4. Discussion

4.1. Heavy Metal Pollution Status and Risk Assessment of Cultivated Soil in Ningxia

Ningxia, a significant agricultural region in northwest China, has witnessed a notable trend towards scale and distinctive characteristics in agricultural development in recent years. However, the prolonged application of agricultural inputs and the rapid urbanization at the county level have led to the emergence of heavy metal pollution issues in cultivated soil within certain irrigation areas. The ranking of over-standard rates is as follows: Cd (98.7%) > Hg (80.1%) > Pb (77.5%) > Cr (47.6%) > As (21.5%). The notably high over-standard rates suggest varying degrees of human-induced impacts on As, Hg, Pb, Cd, and Cr, with Cd, Hg, and Pb showing particularly significant accumulation, mirroring the broader pollution scenario observed in cultivated soil across China. The study findings reveal that the heavy metal pollution in Ningxia’s cultivated land exhibits characteristics of “localized distribution and clustered occurrences.” The pollution hotspots are predominantly situated in the northwest and central regions of Ningxia, primarily around the outskirts of Shizuishan, Yinchuan, Wuzhong, and other longstanding industrial zones, as well as in areas with extensive historical high-intensity cultivation within the Yellow River irrigation zone. The sources of pollution can be attributed to past industrial discharges, sewage irrigation practices, and human activities such as excessive utilization of plastic film, pesticides, and fertilizers. These factors have led to the accumulation of heavy metals, particularly Cd and Hg, in the cultivated soil of Ningxia. Additionally, Non-point agricultural inputs of Cd (e.g., fertilizers and other agro-inputs) result in a widespread, relatively uniform uplift of background levels. By contrast, Hg and Pb arise mainly from industrial, combustion, and smelting emissions, yielding more pronounced hotspot–coldspot mosaics and lower area-wide means than Cd, Consequently, cropland soils exhibit the accumulation hierarchy Cd > Hg > Pb.

Based on the current pollution scenario, Cd and Hg are the predominant contaminants in cultivated soil in Ningxia. It is imperative to enhance ongoing monitoring of soil sites, establish prompt emergency monitoring protocols, promptly identify emerging pollution and diffusion risks, and implement tailored safety measures for the sustainable management of heavy metal-contaminated soil. These actions, informed by the ecological risks associated with heavy metal pollution in soil and the sources of such pollution, are essential for safeguarding the environmental integrity of cultivated soil in Ningxia and ensuring the safe production of agricultural goods.

4.2. Analysis of Heavy Metal Sources in Cultivated Soil of Ningxia

The fragile agricultural ecological environment in Ningxia is characterized by low soil fertility and a risk of heavy metal accumulation, making the analysis of heavy metal pollution sources in cultivated land is crucial for enhancing agricultural productivity. Through Pearson analysis, it was revealed that the salt content in Ningxia’s cultivated soil exhibited a significant negative correlation with four heavy metals [42]. This phenomenon can be attributed to certain anions present in salt can form soluble complexes with heavy metal ions, thereby decreasing the adsorption tendency of heavy metals by soil solids and increasing their solubility and mobility in the solution [43,44]. Conversely, a notable positive correlation was observed between soil organic matter and the four heavy metals, Soil particles with low organic matter content carry fewer net negative charges, making it challenging for them to bind with positively charged heavy metals [45]. This circumstance may result in some free heavy metal ions in the soil solution being absorbed by plants. Additionally, this observation aligns with the significant positive correlation between CEC and the four heavy metals as indicated by the Pearson analysis [46,47], the high CEC can capture heavy metal cations through electrostatic adsorption, thereby reducing their free concentration in the soil solution [48]. Higher pH values and alkaline cation content favor metal accumulation [49,50].

Based on Pearson analysis, PCL and PMF model analysis, 820 cultivated soils were classified into three groups based on heavy metal content [51]. The first group comprised As, Pb, and Cr, originating mainly from a combination of transportation sources and natural parent materials [52]. The findings indicated that As and Pb were primarily derived from automobile exhaust emissions and soil parent materials, entering cultivated soil through atmospheric deposition and rain leaching. Cr in cultivated soil predominantly originated from the weathering of soil-forming parent materials, explaining the spatial distribution patterns of As, Pb, and Cr in the study. In the first component (PC₁), with higher loading values, the contribution rates of the three components were 62.5%, 46.1%, and 76.2%, respectively, showing significant correlations among the three heavy metals, suggesting similar migration patterns and sources. Furthermore, Cr, Pb, and As exhibited minimal spatial variation, indicating their retention of the original natural state in the soil, primarily influenced by parent materials. Category II focused on Hg, primarily sourced from industrial activities. Hg exhibited the highest factor loading (0.956) in the second component (PC₂), contributing 85.70% of the variance. Hg displayed the largest coefficient of variation (0.47), indicating that Hg pollution in cultivated soil primarily stemmed from natural sources and intense human activities [52,53], posing direct threats to the safety of agricultural products. The spatial distribution of sampling points indicated the presence of numerous factories and enterprises surrounding the Hg-polluted cultivated land, particularly concentrated processing enterprise bases in highly polluted areas, attributing Hg accumulation in cultivated soil to industrial production activities [54]. The strengthening of the industrial development model of “agglomeration” in northern Ningxia, particularly the dispersion of smelting dust from coal-fired power generation, oil production, and garbage incineration enterprises into farmland through atmospheric, wet, or dry deposition, resulted in Hg accumulation, consistent with the spatial distribution characteristics of Hg. Category III focused on Cd, primarily originating from agricultural activities. In the third principal component (PC₃), Cd exhibited the highest factor loading value (0.990), contributing 72.1% of the variance, with substantial spatial variation (0.30), indicating significant human-induced influences on Cd levels, widely distributed in high-value areas across the study area. The findings indicated that Cd in cultivated soil primarily resulted from agricultural practices, with excessive use of chemical and organic fertilizers leading to Cd accumulation. Long-term production of microplastics from agricultural residual film was positively correlated with heavy metal accumulation [54], contributing to Cd pollution in cultivated soil over time.

5. Conclusions

(1)

The concentrations of five heavy metals in cultivated soil in Ningxia were below the threshold values for agricultural soil pollution risk. However, the average levels of Cd, Pb, and Hg exceeded the background levels of Ningxia soil, with Cd and As approaching the threshold values for agricultural soil pollution risk. Given that heavy metals are significant contributors to adult carcinogenic risk [54], continuous long-term monitoring is essential.

(2)

The single-factor index method and Nemerow comprehensive pollution index method indicated that, overall, the cultivated soil in Ningxia was deemed clean. However, Cd and Hg elements still exhibited medium to high potential ecological risks. The cumulative index analysis revealed that Cd and Hg are the primary heavy metal pollutants in Ningxia’s cultivated soil, posing significant toxicity levels that can adversely impact plant health across various pollution levels [55], Particular concern is the compounded pollution of agricultural land due to the synergistic effects of emerging contaminants like microplastics and antibiotics, in addition to heavy metals, retained in the agricultural production processes.

(3)

The spatial distribution patterns of heavy metals in cultivated soil in Ningxia exhibited distinct characteristics. Arsenic (As) and Chromium (Cr) displayed continuous high concentrations in the northern and western regions of the study area. Mercury (Hg) exhibited persistent high levels in the northern and eastern parts of the study area. Cadmium (Cd) showed continuous high concentrations in the central region, with elevated levels also observed in certain areas in the northern and southern parts of the study area. Lead (Pb) concentrations were predominantly high in the central and northern regions of the study area.

(4)

A notable inverse relationship was observed between soil salinity and heavy metal concentrations in cultivated soil, while a substantial positive correlation was noted between soil cation exchange capacity and heavy metal levels in the same soil [56]. Analysis using Pearson correlation, principal component analysis (PCA), and positive matrix factorization (PMF) indicated that arsenic (As), lead (Pb), and chromium (Cr) predominantly originated from a combination of transportation activities and natural parent materials [57,58], mercury (Hg) primarily originated from industrial sources [59], and cadmium (Cd) mainly originated from agricultural activities [60,61,62]. Accordingly, we recommend source-specific mitigation and long-term surveillance to manage cumulative risks.