Mitigation strategies for soil acidification based on optimal nitrogen management

Highlights

● Soil acidification is determined by proton production and soil buffering capacity.

● Cropland acidification is mainly caused by anthropogenic activities.

● Nitrogen transformations dominate anthropogenic soil acidification processes.

● Acidification stage-specific strategies are needed for managing soil acidification.

● Optimizing N rate and N form is highly effective in mitigating soil acidification.

Abstract

Soil acidification is a serious constraint to food production worldwide. This review explores its primary causes, with a focus on the role of nitrogen fertilizer, and suggests mitigation strategies based on optimal N management. Natural acidification is determined by the leaching of weak acid mainly caused by climate and soil conditions, whereas the use of ammonium-based fertilizers, nitrate leaching and removal of base cations (BCs) by crop harvesting mostly accounts for anthropogenic acidification. In addition, low soil acid buffering capacity, mainly determined by soil parent materials and soil organic matter content, also accelerates acidification. This study proposes targeted mitigation strategies for different stages of soil acidification, which include monitoring soil carbonate content and pH of soils with pH > 6.5 (e.g., calcareous soil), use of alkaline amendments for strongly acidic soils (pH < 5.5) with aluminum toxicity risk to pH between 5.5 and 6.5, and decreasing acidification rates and supplementing BCs to maintain this optimal pH range, especially for soils with low acid buffering capacity. Effective mitigation involves optimizing the rate and form of N fertilizers used, regulating N transformation processes, and establishing an integrated soil–crop management system that balances acid production and soil buffering capacity.

Graphical abstract

Keywords

Soil acidification / nutrient management / nitrogen / soil buffering capacity

1 Introduction

Soils are vital for terrestrial ecosystem and support terrestrial life on the planet^[1,2], and healthy soils are critical for global food production and human well-being^[3]. However, around 33% of the global arable land is moderately to highly degraded, with soil acidification being one of the primary types^[4]. It affects approximately 30% of the total ice-free land area and as much as 50% of potential arable land^[5]. Soil acidification causes various conditions that restrict crop growth, which include decreased soil fertility with decreased availability of phosphorus and base cations (BCs) such as calcium, magnesium and potassium^[6], and the release of toxic aluminum and manganese^[7]. Also, soil acidification enhances the availability of toxic heavy metals, especially lead and cadmium, increasing the risk of their accumulation in crops and animals affecting food quality and human health through the food chain^[8,9].

1.1 Definition of soil acidification

Soil pH is a measure of the H⁺ concentration in the soil solution, and it serves as a key predictor of soil biology, chemistry, and physical processes, directly affecting plant growth and development^[10]. The United States Department of Agricultural National Resources Conservation Service has categorized soil based on its pH as extremely acidic (< 4.5), very strongly acidic (4.5–5.0), strongly acidic (5.1–5.5), moderately acidic (5.6–6.0), slightly acidic (6.1–6.5), neutral (6.6–7.3), slightly alkaline (7.4–7.8), moderately to strongly alkaline (7.9–9.0), and very strongly alkaline (> 9.1)^[11]. Most agricultural plants grow optimally when soil pH falls between 6 to 8, and the optimal availability for most of the nutrients is found in the slightly acid pH range^[12]. Soil pH is calculated by the negative logarithm of the H⁺ concentration in soil solution when the soil solid-liquid phase is in equilibrium. In this context, soil pH only represents the active protons in soils, neglecting the exchangeable acidity held near clay and humus surfaces^[13], as well as the residual acidity, representing the H⁺ and Al³⁺ bound on the clay and humus surfaces^[14]. These latter forms of acidity constitute potential acidity, which is usually quantitatively greater than active acidity^[14]. The amount of potential acidity is mostly determined by the soil pH and cation exchange capacity (CEC) and it increases substantially as pH drops below 5.5, mainly due to increased exchangeable acidity^[15]. Consequently, total soil acidity hinges not only on soil pH but also on cation holding capacity, which encompasses exchangeable and residual acidity.

1.2 Buffering mechanism of soil acidification

Soil acidification is generally indicated by a decrease in soil pH. However, the change in soil pH is usually smaller than the amount of proton input from external sources, primarily due to the existence of acid-buffering substances within the soil. Therefore, soil acidification is defined as a decrease in acid neutralizing capacity of the solid phase of soil, which is conceptually defined as the sum of basic components minus the strongly acidic components at the reference pH of soils (generally pH 2.0–5.0)^[16].

Acid buffering processes and the buffering capacity of soil solid phase substances differ as pH changes (Tab.1)^[6,17]. When the soil pH drops from 8 to around 3.5, it generally goes through a carbonate buffer system, a BC exchangeable buffer system, and a hydroxy aluminum and a hydroxy iron buffer system. When the soil is in the carbonate buffer system, it takes about 100 years to consume 1% calcium carbonate under natural conditions^[18,19]. The buffering capacity is about 1500 keq·ha^–1 H⁺ in a calcareous soil per 1% CaCO₃ content in a soil with a weight of 15 kt (Tab.1). Therefore, a calcareous soil can generally maintain a high soil pH of 7.0–8.5 for a long period. However, when the carbonate in the soil is exhausted, entering the BC exchange buffer system, the acid buffering capacity can be as low as 250 keq·ha^–1 H⁺. When the soil enters the buffer system of aluminum hydroxide and iron hydroxide (pH < 5.0), the buffering capacity increases to 1000–1500 keq·ha^–1 H⁺ per % clay. This indicates that the main acid buffering systems of both calcareous soil and very strongly acidic soil (pH < 5.0) generally have a strong buffering capacity, thereby the soil pH is insensitive to H⁺ input, whereas the pH of soils in the BC exchange system (pH 5.0–7.0) is more sensitive to H⁺ addition, as the dominated acid buffering element is BCs^[20]. Therefore, the global soil pH at 0.5 m depth has two types of buffering systems approximately at pH 8.2 and 5.1 regulated by CaCO₃ and Al(OH)₃ buffers, respectively^[21].

Tab.1 Main buffering systems and their buffering capacity in different soil pH ranges

pH range	Main buffering system	Buffering capacity*
6.2 < pH < 8.6	Carbonate	1500 keq H+ per % CaCO3
5.0 < pH < 6.2	Base cation (BC) exchange#	250–750 keq H+ per % (primary) silicate
pH < 5.0	Hydroxy-aluminum	1000–1500 keq H+ per % clay
pH < 3.8	Hydroxy-iron	Lacking data

Note: *The acid buffer capacities were based on a soil weight of 15,000 t, calculated by assuming a bulk density of 1500 kg·m−3, expressed ha−1 and 1 m−1 soil depth[6]. #More specifically, the weathering of silicate minerals dominates the buffer reaction when soil pH > 5.0 as H+ and Al3+ ions replace the BCs on the exchange complex[17].

2 Causes and processes of soil acidification

2.1 Causes of soil acidification

Causes of soil acidification can be categorized into the following aspects.

Natural soil acidification. Naturally, H⁺ production occurs when a weak acidic anion is formed, such as the dissolution of CO₂ to form carbonic acid (H₂CO₃) and the dissociation of carboxylic acids (RCOOH) produced by plants and microorganisms^[22]. Dissolution of H₂CO₃ and RCOOH releases H⁺ exchanging with BCs, which is then leached to the subsoil accompanied with HCO₃^– and RCOO^– by excess precipitation, being the main contributor to the natural forest soil and grassland, especially for the humid forested ecosystem. For example, Fujii et al.^[23] found that RCOO^– dominated the anions fluxes in the O horizon of the Japanese forest soil, being the most important driver of soil acidification. Natural acidification is the main driver in soils with high organic carbon content as in brown and dark brown soils in north-eastern China^[24] and those with high pH or under high CO₂ pressure as in calcareous soils in the Netherlands; however, it has minor acidifying effects in non-calcareous soils^[18].

Anthropogenic soil acidification. Without any human intervention, soil acidification is a naturally slow process. It was estimated that the pH of red soil declined by 1 unit after 2.3 million years without artificial disturbance^[25]. However, the soil acidification rate has been greatly accelerated by human activities, such as burning fossil fuels causing atmospheric acid deposition, application of acidifying fertilizers (including neutral fertilizers like urea but with acidifying effects) and nutrient removal through harvested parts of crops.

Atmospheric acid deposition. From the beginning of the Industrial Revolution, emissions of acidifying compounds such as sulfur dioxide (SO₂) and nitrogen oxides (NO_x) greatly increased due to the rapid industrial development. Consequently, atmospheric acid deposition has become a serious global environmental problem, elevating the acidity of precipitation and acidification of soils and lakes in Europe and North America^[26]. In forest soils in the UK, a 1.5-unit decline in topsoil pH (0–23 cm) was found during 1904–1964, mostly driven by the elevated atmospheric acid inputs caused by SO₂ and NO_x emissions (from 0.8 to 2.6 kmol·ha^–1) and N transformations (from 0.6 to 2.9 kmol·ha^–1)^[27]. In the regions of southern Sweden (Europe) and the USA (North America) where SO₄-S deposition declined, there had been slow recovery of the soils from acidification^[28,29]. However, in some areas in Asia, though strict regulations have declined the total S deposition, there was a delayed recovery of soil from acidification as N deposition-induced soil acidification has increased, either due to the increase in N deposition^[30] or increase in NH₄⁺/NO₃^– ratio in N deposition caused by intensive agricultural activities^[31].

Acidifying fertilizers. In agricultural systems, the increase in N fertilizer application has increased food production but also increased acidification risks. Nearly all processes in the N cycle affect H⁺ production or consumption. Overuse of N fertilizers, in particular ammonium-based (NH₄-N) fertilizers, caused significant soil acidification on major Chinese croplands^[32]. The application of NH₄-N fertilizers greatly increased soil acidification due to the enhanced net H⁺ production by nitrification. Also, leaching of NO₃^– results in permanent acidification by accompanying soil BCs (the decrease in soil buffering capacity). It was observed in the Park Grass Experiment at Rothamsted in Hertfordshire, England that ammonium sulfate application caused a rapid decrease in pH, starting in the surface soil but occurring throughout the profile to at least 1 m deep, compared to the treatment without any fertilizer application^[33,34].

Nutrient removal by crops. To maintain the inherent charge balance, crops release H⁺ to soil solution when absorbing cations more than anions and vice versa^[35]. The removal of cations through harvested parts permanently decreases soil buffering capacity (BCs losses) and releases H⁺ when the uptake of anions is less. The acidifying effects vary between crop types due to different amount and composition of nutrients in the harvested component. For cereal crops, crop-induced acidity can vary from 0.25 to 0.76 mol·kg^–1[35], whereas fruits and upland crops generally have higher ratios of BCs/anions uptake than, for example, paddy rice^[36]. For grain legumes, apart from the fixed N and enhanced N-induced acidification, crop-induced acidity can be as high as 1.77 mol·kg^–1[35], thereby appearing highest acidifying potential. Bolan and Hedley reported that, where legumes had been grown continuously in Australia for > 30 years, soil pH declined by 1 unit^[22].

2.2 Main processes causing soil acidification

In the soil–plant system, nutrient transformations and element cycles generate proton or hydroxyl ion (equal to H⁺ consumption). The most important elements include C, N, cations (BCs and Al³⁺) and anions (H₂PO₄^–, SO₄^2–, and Cl^–)^[37], other elements with minor effects are not discussed here; the processes are listed in Tab.2.

Tab.2 Some reaction equations of H+ production and consumption processes in the carbon, nitrogen, cation, and anion cycles

Process	Reaction equation
Carbon cycle
- Dissociation of CO2	${\mathrm{C}\mathrm{O}}_2+{\mathrm{H}}_2\mathrm{O}\leftrightarrow {\mathrm{H}\mathrm{C}\mathrm{O}}_3^{-}+{\mathrm{H}}^{+}$
- Dissociation of organic acids (ROOH)	$\mathrm{R}\mathrm{C}\mathrm{O}\mathrm{O}\mathrm{H}\leftrightarrow {\mathrm{R}\mathrm{C}\mathrm{O}\mathrm{O}}^{-}+{\mathrm{H}}^{+}$
Nitrogen cycle
- N fixation	$2{\mathrm{N}}_2+3\mathrm{C}{\mathrm{H}}_2\mathrm{O}+4\mathrm{R}\mathrm{O}\mathrm{H}\to 4\mathrm{R}\mathrm{N}{\mathrm{H}}_2+3\mathrm{C}{\mathrm{O}}_2+{\mathrm{H}}_2\mathrm{O}$
- Mineralization of organic N	${\mathrm{R}\mathrm{N}\mathrm{H}}_2+{\mathrm{H}}^{+}+{\mathrm{H}}_2\mathrm{O}\leftrightarrow \mathrm{R}\mathrm{O}\mathrm{H}+{\mathrm{N}\mathrm{H}}_4^{+}$
- Volatilization of NH3	${\mathrm{N}\mathrm{H}}_4^{+}\leftrightarrow {\mathrm{N}\mathrm{H}}_3+2{\mathrm{H}}^{+}$
- Nitrification	${\mathrm{N}\mathrm{H}}_4^{+}+2{\mathrm{O}}_2\to {\mathrm{N}\mathrm{O}}_3^{-}+2{\mathrm{H}}^{+}+{\mathrm{H}}_2\mathrm{O}$
- Uptake of $\mathrm{N}{\mathrm{O}}_3^{-}$	$\mathrm{R}\mathrm{O}\mathrm{H}+{\mathrm{N}\mathrm{O}}_3^{-}+{\mathrm{H}}^{+}+2\mathrm{C}{\mathrm{H}}_2\mathrm{O}\to \mathrm{R}\mathrm{N}{\mathrm{H}}_2+2\mathrm{C}{\mathrm{O}}_2+2{\mathrm{H}}_2\mathrm{O}$
- Denitrification	$5\mathrm{C}{\mathrm{H}}_2\mathrm{O}+4{\mathrm{N}\mathrm{O}}_3^{-}+4{\mathrm{H}}^{+}\to 2{\mathrm{N}}_2+5\mathrm{C}{\mathrm{O}}_2+7{\mathrm{H}}_2\mathrm{O}$
Anion cycle
- Plant uptake of anions (An–, e.g., $\mathrm{S}{\mathrm{O}}_4^{2-}$, ${\mathrm{H}}_2\mathrm{P}{\mathrm{O}}_4^{-}$, Cl–)	$\mathrm{R}\mathrm{O}\mathrm{H}+{\mathrm{A}\mathrm{n}}^{-}+{\mathrm{H}}^{+}+\mathrm{C}{\mathrm{H}}_2\mathrm{O}\to \mathrm{R}\mathrm{H}-\mathrm{A}\mathrm{n}+\mathrm{C}{\mathrm{O}}_2+{\mathrm{H}}_2\mathrm{O}$
- Soil absorption of An–	${\left(\mathrm{O}\mathrm{H}\right)}_{\mathrm{e}\mathrm{x}}+{\mathrm{A}\mathrm{n}}^{-}+{\mathrm{H}}^{+}\to {\mathrm{A}\mathrm{n}}_{\mathrm{e}\mathrm{x}}^{-}+{\mathrm{H}}_2\mathrm{O}$
Cations cycle
- Plant uptake of cations (M+, e.g., Ca2+, Mg2+, K+)	$\mathrm{R}\mathrm{C}\mathrm{O}\mathrm{O}\mathrm{H}+{\mathrm{M}}^{+}\leftrightarrow \mathrm{R}\mathrm{C}\mathrm{O}\mathrm{O}\mathrm{M}+{\mathrm{H}}^{+}$
- Soil adsorption of M+	${\mathrm{M}}^{+}+{\mathrm{H}}_{\mathrm{e}\mathrm{x}}^{+}\leftrightarrow {\mathrm{M}}_{\mathrm{e}\mathrm{x}}^{+}+{\mathrm{H}}^{+}$

3 Main factors affecting soil acidification in cropland

Soil acidification of cropland has gained wide attention since Guo et al.^[32] reported the significant acidification in Chinese croplands. Characters of cropland acidification are greatly different from natural ecosystems because of intensive disturbance of nutrient cycles by fertilizer and water management^[38]. Overall, the main factors affecting soil acidification rates in cropland are: (1) fertilizer application (in particular N), (2) crop harvest, and (3) soil acid buffering capacity.

3.1 Fertilizer application

N fertilizer application is one of the most important contributors to soil acidification. China is the largest synthetic N fertilizer consumer in the world, where the N use efficiency (N removal by crop harvests divided by total N input) is lower than 50%, indicating that over half of N input was lost^[39]. The overuse of N fertilizers caused soil pH to decline by 0.5 units during the 1980s–2000s in major Chinese croplands^[31]. This acidification rate was much faster than previous findings in the forest soils of Europe caused by acidic deposition in the 1980s^[27,34] but was quite comparable with intensely managed agricultural and grassland soils of Australia^[40]. Globally, N addition significantly decreased soil pH by 0.26 on average^[41]. More recent studies also found that N fertilizer input can lead to extremely serious soil acidification in tea plantations and grassland systems^[42,43].

N fertilizer application significantly enhances soil acidification by affecting the cycling of H⁺ in the soil–plant system. N form is important in the degree acidification caused. Common mineral N fertilizer types include urea, liquid ammonia, ammonium bicarbonate and ammonium sulfate. These fertilizers can be categorized into three types based on the N form of their main substances: non-charged N (such as urea and liquid ammonia), ammonium-based N and nitrate-based N. In addition to the different amounts of H⁺ contributed by N transformations, the selective uptake of NH₄⁺ and NO₃^– also affects the soil acidification process (Fig.1).

Fig.1 Processes of N transformations associated with soil acidification. The process in red label indicates that it produces H+ and in black consumes H+.

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Ammonium-based fertilizers pose the greatest acidification risk due to the nitrification process (conversion of NH₄⁺ to NO₃^–) and subsequent NO₃^– leaching. Theoretically, the nitrification of 1 mol of NH₄⁺ to form 1 mol of NO₃^– produces 2 mol of H⁺. If the produced NO₃^– is taken up by plants, it releases 1 mol of OH^–, and overall 1 mol of NH₄⁺ applied to soils produces at least 1 mol of H⁺, regardless of whether the NH₄⁺ is taken up by plant (either in the form of NH₄⁺ or NO₃^– after nitrification) or absorbed by soils or even lost to air as NH₃. However, if the NO₃^– is fully leached, 1 mol of NH₄⁺ would produce 2 mol of H⁺. Consequently, in well-ventilated sandy soil, the nitrification of NH₄⁺ and the subsequent leaching of NO₃^– have the greatest impact on soil acidification^[44].

Compared to ammonium-N fertilizers, liquid ammonia and urea have relatively lower acidification capacity, as their conversion to NH₄⁺ consumes the same amount of H⁺. In the case of organic manure, the acidification ability of N is the same as that of urea because of the same form of N; organic manure, however, can alleviate soil acidification due to high BCs content. Generally, nitrate-N fertilizers do not produce H^+[45] and when plants uptake 1 mol of NO₃^–, equal amount of H⁺ is released, resulting in an increase in soil pH in the rhizosphere^[46]. The same happens with the denitrification of NO₃^– to N gases (N₂, NO, and N₂O). In summary, N fertilizer types have different impacts on soil acidification, with the ranking as follows: ammonium-N fertilizer > non-charge fertilizer > nitrate-N fertilizer. It is worth noting that when urea and NO₃^– are used, theoretically soil pH hardly changes or may even increase following NO₃^– uptake.

Numerous long-term field experiments have consistently demonstrated the impacts of N fertilizers on soil acidification. In the Park Grass experiment, (NH₄)₂SO₄ application for 150 years decreased soil pH by 1.7 units compared to unfertilized treatment. In contrast, the application of sodium nitrate increased soil pH by 0.7 units^[34]. Khonje et al.^[47] found that the soil acidification rates associated with nine annual applications of the N fertilizers at 300 kg·ha^–1 N was of the order: (NH₄)₂SO₄ > NH₄Cl > anhydrous NH₃ = NH₄NO₃ > urea > Ca(NO₃)₂ = NaNO₃. Many long-term trial sites in China also showed that N fertilizer application increases soil acidification^[44,48]. For example, the pH of red soil treated with urea for 18 years decreased by more than 1 unit compared to the control (unfertilized) plot located in southern China^[49]. Yang et al.^[42] found marked soil pH decline in both topsoil (0–40 cm) and subsoil (40–90 cm) at a relatively high N application rate (569 kg·ha^–1), being from 4.16 to 3.15 and from 3.67 to 3.35, respectively, over 8 years compared to the control without N application^[42].

A recent study revealed that N fertilizer application contributed more than 55.1% of H⁺ production between the 1980s and the 2010s in Chinese croplands^[50]. The high contribution of N cycling to soil acidification in China can be explained for two reasons. First, the increasing application of N fertilizer has greatly exceeded crop demand over the past 20 years^[51] (see also Fig.2). The average N surplus (total N input minus crop uptake) of major crops (including cereal crops and cash crops) varied from 133 to 429 kg·ha^–1 according to a national scientific fertilizer application survey data set in 2019. Secondly, the changing fertilizer type also contributed to the N-induced acidification. Urea and compounded N (often in urea form) are the main forms of N fertilizer in China, accounting for over 87% in 2020, and nitrate-based nitrogen fertilizer only accounted for less than 3.5%, according to International Fertilizer Association. The structure of the N fertilizer form has significantly changed from the 1980s when the ammonia bicarbonate dominated in N fertilizer. In other words, the N fertilizers applied are still dominated by acid-type N fertilizers.

Fig.2 Fertilizer use of major crops in China during 1998–2018. The amount indicates the sum of N, P2O5, and K2O (kg·ha–1). The sugar crop includes sugarcane and sugar beet and oil crop includes peanuts, rapeseed, sesame, soybeans, and sunflower. Values are means for each crop.

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3.2 Crop harvest and residue management

The plant-induced soil acidification mainly includes two aspects: (1) net H⁺ production by the plant due to excess uptake of non-N cations over non-N anions^[35]; and (2) removal of BCs (e.g., Ca, Mg, and K) in harvest parts such as grain, straw and hay decreasing soil buffering capacity. In agriculture systems, biomass harvesting is unavoidable, but returning crop residues, as much as possible, is potentially beneficial for minimizing soil acidification induced by crop removal^[52,53]. The uptake of the BCs presents in the form of companied cations and organic anions in plants (Tab.2), and the localized net H⁺ production is balanced by the release of hydroxyl ions during subsequent plant decomposition. In other words, the contribution of plants to soil acidification is close to zero in the case of whole plant biomass returned to the soil, since no BCs removal occurs but net carbon input from the biomass. The returned carbon potentially increases soil organic carbon content and CEC, therefore increasing soil buffering capacity. Therefore, continuous removal of harvested parts (for crops) from the field causes permanent soil acidification, and the net impact keeps increasing as the aboveground biomass increases. It is noteworthy that excess uptake of cations over anions often occurs more in leaves or stems than grains. For this reason, soil acidification is faster under continuous removal of both grain and straw than when grain only is harvested^[54].

3.3 Soil acid buffering capacity

Apart from external factors (e.g., acid deposition and fertilizers), soil acid buffering capacity also affects the soil acidification progress, which is naturally determined by parent materials and the amount of soil organic matter (SOM) presents. Different parent materials lead to distinct soil physical, chemical and biological properties, which in turn alter soil buffering capacity and acidification processes^[55]. When the soil contains free carbonate (e.g., CaCO₃), every mole of carbonate can neutralize 2 mol of H⁺, therefore the buffering capacity of calcareous soils is determined by the content of carbonate within the soil. As soils move to the BC buffering system, soil CEC controls the absorption and supply of exchangeable cations in the soil, which is mostly contributed by SOM and clay^[56]. Higher CEC indicates that the soil has more exchangeable sites to absorb H⁺ and Al³⁺ from the soil solution avoiding the decrease in soil pH, and the soil is capable of providing more BCs to buffer excess H⁺ input. Soils that developed from granitic parent materials are likely to be more acidic than soils derived from alluvial sediments partly due to their low SOM content and thus decreased exchange capacity for BCs^[57]. Also, the composition of clay minerals is closely related to soil buffering capacity. The 2:1 type phyllosilicate mineral has more isomorphous substitution, resulting in permanent negative charges in soils that can adsorb BCs and thus have a large acid buffering capacity than the 1:1 type phyllosilicate with little or no isomorphous substitution^[58]. Additionally, soil texture is also an important factor in controlling soil acidification rates. When the soil sand content is higher, the potential leaching of mobile anions such as NO₃^–, Cl^–, and SO₄^2– is also higher, causing greater soil acidification under similar fertilizer management^[59].

In conclusion, there are three main factors that cause soil acidification in modern agriculture. Firstly, the excessive application of N fertilizers, especially ammonium-N fertilizers, increases NO₃^– leaching from the soil accompanied by BCs, resulting in large amounts of H⁺ remaining in the soil. This also occurs with the overuse of S fertilizers. Secondly, the continuous removal of harvested crops depletes soil BCs, exacerbating the loss of soil acid buffering capacity. Additionally, cultivation of certain crops can increase soil acidification. For example, legumes produce and accumulate most of its N through N₂ fixation and the large input of N from legumes into soils increases NO₃^– leaching. Lastly, the soil acid buffering capacity, largely affected by factors such as the content of SOM and clay minerals, determines soil sensitivity to acidification processes. Soils with low levels of SOM and clay minerals tend to have a lower acid buffering capacity, and are more prone to acidification at a faster rate.

4 Mitigation strategies of soil acidification based on optimal nitrogen management

Soil acidity limits food production in many major agricultural production regions globally^[4]. As N fertilizer is one of the most important factors exacerbating soil acidification, we propose effective and sustainable mitigation strategies for soil acidification based on optimal N management which can be achieved by carefully designed, region-specific optimization of N management, as discussed below.

4.1 Classified management scheme for soil acidification

Soil acidification accompanies gradual consumption of soil carbonate until it is consumed fully before the soil moves to the next buffering stage of BC exchange system and then to hydroxy aluminum/iron buffer system. This is reflected by the carbonate and exchangeable BCs losses, decrease in soil pH and increase in exchangeable Al to toxic level, thereby stunting growth or even crop failure^[60–62]. Considering the ultimate target of sustainable crop production and sustainable land use, we propose a crop management scheme including three major soil buffering stages, that focuses on decreasing soil acidification rates, enhancing soil acid buffering capacity and alleviating the damage caused by acidification (Fig.3).

Fig.3 Mitigation strategies for sustainable management of cropland acidification.

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The application of one or multiple mitigation principles and strategies is based on the nature and extend of the acidification problem, soil buffering capacity and the intrinsic characteristics of the soil buffering system in different ranges of soil pH. Giving attention to all these aspects is critical to make the solution effective. Note that while the soil buffering stage classification is arbitrary, they are based on sound knowledge of soil acidification and its management practices. We also assumed that, in most cases, the slightly acid soils (pH ranging from 5.5 to 6.5) are optimal for crop production. Also, it is important to note that care should be taken when defining critical/target soil pH for crop yields, as the measure soil pH will be dictated by the soil extractant, for example, soil pH of soil water extract is higher than that of CaCl₂ soil extract^[63].

In soils with a pH above 6.5, generally categorized as non-acidic and slightly alkaline, the pH remains relatively stable due to the high acid buffering capacity of carbonate. In such soils, soil acidification has negligible or positive effects on crop growth. However, in the long run, continued acidification poses a risk to even such soils when the buffering materials (mainly carbonate) are exhausted. For example, a study has revealed that long-term N-induced acidification led to 7 Mha of cropland becoming carbonate-free from 1980 to 2020 in China^[61]. Therefore, regular monitoring of soil quality, especially the carbonate content and soil pH by establishing fixed observation points is crucial in this stage of acidification to avoid potential acidification risks. However, considering that acidification may deplete soil inorganic carbon stock, lowering soil acidification rates by optimizing N form and input rate will be valuable even in this context.

In slightly acidic soil with a pH ranging from 5.5 to 6.5, soil acidification accelerates the losses of BCs causing substantial decline in soil fertility, which negatively affects crop growth. Hence, the primary objectives of measures at this stage aim to lower the soil acidification rate and supply the lost BCs, increasing the acid buffering capacity. These key measures include: (1) optimizing the form and amount of N fertilizers to minimize soil acidification caused by N fertilizer^[64]; and (2) increasing the input of alkaline materials, such as crop straw, manure and biochar, rich in BCs, preventing soil acidification and enhancing soil buffering capacity^[65]. The lower threshold pH for this stage is around 5.5, slightly higher than the turning point pH (~5.0) between the BC exchange and aluminum buffering systems because most field crops fail to obtain the maximum yield when soil pH is 5.0 or lower^[63].

When the soil pH is below 5.5, soil acidification generally starts to decrease crop yield because of poor soil fertility (e.g., low Ca and Mg content due to large loss of BCs) and the toxicity caused by increasing levels of Al³⁺ and Mn^2+[60]. Priority measures at this stage should focus on raising soil pH quickly by alkaline amendment, for example, the application of lime or other alkaline substances to increase soil pH to ensure optimal crop production^[66], or crop selection which increases the tolerance to elevated Al³⁺. However, minimizing soil acidification rates is still essential, since it is not practical to apply high rates of alkaline substances considering the cost^[67], as well as potential re-acidification after liming^[68]. Therefore, decreasing soil acidification rates through optimize N fertilizer form and rate, and improving acid buffering capacity by increasing the input of organic manure or straw are also required to guarantee sustainable crop production and soil quality.

4.2 Optimizing nutrient management to mitigate soil acidification

China is a major contributor to the global food systems; however, nearly 20 Mha (47%) of croplands are acidic (pH < 6.5), mostly in southern China^[69]. A recent study made an alarming observation that if the current nutrient management practices continue, future production losses due to soil acidification will be about 16% or more by 2050^[70] even if the “Action Plan for Zero Growth of Fertilizer Use by 2020” remains in force. Since N cycling is the main factor exacerbating soil acidification, nutrient management measures based on N regulation are crucial for acidification management. The effective measures include optimizing the N application rate, managing N forms, optimizing N transformation processes and practicing an integrated soil–crop system management as shown in Fig.4.

Fig.4 Mitigation strategies for sustainable N management of cropland acidification.

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Optimize the N application rate. The optimal N application rate based on crop N demand should be considered first. Currently, crop N use efficiency in China is only about 40%, which could be increased to 60%–70% to maintain soil fertility and decrease environmental costs^[71,72], implying a great operational space for decreasing N application. It was estimated that the N fertilizer use in China could be decreased from 27 Mt in 2020 to 21 Mt in 2060 toward an ambitious environmentally sustainable land-use transformation pathway^[73]. Different crops have different potential to decrease N application in China. For example, the N input can be decreased by 21% to 28% in cereal crops (maize, rice, and wheat)^[74], and a projected 38% decrease in the N application rate can be achieved for vegetables based on root zone N management without compromising the vegetable yield compared to conventional N fertilizer use^[75]. Fruit systems have higher N inputs with lower N use efficiency, in which over 60% of N inputs can be eliminated if N management based on crop demand is followed^[76]. In general, optimizing N application rate is an effective measure with great potential to decrease soil acidification. A recent meta-analysis showed that decreasing N input in grasslands from 300 to 50 kg·ha^–1·yr^–1 effectively slowed down soil acidification, with pH declining by 0.76 units in 300 kg·ha^–1·yr^–1 compared to 0.30 units in 50 kg·ha^–1·yr^–1 over a 5-year period^[77]. In a field experiment, the acidification rate was decreased by 24% through optimization of urea application, and by 44% through optimization of ammonium-N fertilizer application in a wheat-maize system^[71].

Optimize nitrogen forms. Nitrification is an important process producing H⁺, which can be inhibited to mitigate soil acidification by adjusting fertilizer forms. In general, ammonium-based fertilizers (e.g., (NH₄)₂SO₄ and NH₄Cl) acidify soils greater than urea^[71,77,78]. Hao et al.^[71] showed that the average acidification rate was 10 keq·ha^–1·yr^–1 H⁺ when urea was applied and 41 keq·ha^–1·yr^–1 when NH₄Cl was applied in a wheat-maize double cropping system with a silty loam soil (initial pH was 5.1 in topsoil of 0–20 cm). In contrast, rhizosphere soil pH increased with the application of nitrate-N fertilizers^[46]. Therefore, transforming ammonium-based fertilizers to nitrate-based fertilizers can decrease soil acidification given that most upland crops, such as maize, tobacco, vegetables and wheat, are more effectively grown with nitrate-based fertilizers^[79,80].

In addition, replacing part of N fertilizers with organic N fertilizers is also effective in mitigating soil acidification, as most organic fertilizers are alkaline, directly neutralizing soil acidity and supplying BCs^[81,82]. Also, organic fertilizers raise SOM content, which can effectively improve acid buffering capacity. Research has shown that replacing 50% of mineral N fertilizers by organic N increased the pH buffering capacity of Alfisol by 60% to 81%^[82]. This can also effectively decrease the acidification by inhibiting nitrification of NH₄^+[82,83]. Additionally, unlike mineral fertilizers, nutrients in organic fertilizers are mostly slow-releasing, which lessens nutrient runoffs, help balances crop demand-based nutrient supply, slows the rate of soil acidification and improves soil and environmental quality^[84]. The results of Cai et al.^[64] showed that 40%, or more, of total N from manure can prevent or reverse acidification of red soil, and provide all the P crops required. Apart from organic manure, the combined application of urea and biochar can decrease the nitrification process, thus mitigating soil acidification^[85]. Also, some slow-release or smart fertilizers (e.g., chitosan nanohybrid) can also decrease the N fertilizer application as a compensatory substitute^[86].

Managing nitrogen transformation processes. The nitrification of 1 mol of NH₄⁺ to form 1 mol of NO₃^– produces 2 mol of H⁺. Therefore, it is plausible and effective to control soil acidification by regulating the nitrification process using nitrification inhibitors. Research has shown that adding the nitrification inhibitor DMPP along with N fertilizers increased soil pH, decreased N input by 37% without yield loss, and decreased NO₃^– leaching, promoting sustainable N management in tea plantations^[87]. Also, using nitrification inhibitors can decrease the emissions of N₂O due to the less NO₃ produced^[88]. The combined application of N and P can change N:P stoichiometry and negatively affect the abundance of ammonia-oxidizing bacteria and ammonia-oxidizing archaea, thereby inhibiting the nitrification process of urea in soil^[89]. In addition, incorporating urease inhibitors into fertilizers is also an important technology to decrease N loss. Urease inhibitors can lower the activity of soil urease, slow down the hydrolysis of urea in soils, and decrease the loss of NH₃ volatilization. Individual application or co-application of urease inhibitors, chemical nitrification inhibitors and biochar could mitigate NH₃ volatilization by 12.5%–26.5%, N₂O emission by 62.7%–73.5%, and N leaching loss by 17.5%–49.0% in a wheat growth pot experiment with a calcareous soil developed from purplish shale^[90].

Integrated soil–crop system management. Integrated soil-crop system management often recommends precise fertilizer application combined with optimized field management, which improves the utilization rate of fertilizer and slows down cropland acidification^[91]. For example, optimizing a fertigation system to improve fertilizer application accuracy can decrease N input by 11% on average compared with the traditional irrigation-fertilizer system^[92], slowing the rate of soil acidification. In addition, fertilizer placement close to seeds or plant roots (deep fertilizer placement) ensures high nutrient availability and nutrient use efficiency. A systematic review showed that deep fertilizer placement led to a 3.7% higher yield and 11.9% higher nutrient content in aboveground parts than fertilizer broadcast^[93]. An integrated land-use management system for pasture and agriculture with precise fertilizer application achieve soil nutrient balance and significant decrease in fertilizer use^[94]. Therefore, a combination of precise fertilizer application and optimized field management can improve fertilizer utilization efficiency and decrease fertilizer loss.

5 Conclusions

Soil acidification is one of the most serious threats to global food production and human health. Natural acidification occurs due to the net leaching of bicarbonate and organic acid accompanied by BCs, which is slowly driven by excess precipitation, surpassing soil water loss through evaporation. However, human activities have substantially increased soil acidification in croplands. Application of acidifying fertilizers, especially ammonium-based fertilizers which increases acid production via N transformations, excessive N application causing leaching of nitrate along with BCs, and continuous BCs removal by crops all lead to soil acidification.

Considering the distinct soil acidification status, processes and the rate of progress, different acidification mitigation strategies were proposed for soils with pH of > 6.5, 5.5–6.5, and < 5.5 accordingly. Generally, the soil with a pH > 6.5 have a strong acid buffering capacity, e.g., calcareous soils with free carbonate, which therefore only requires frequent monitoring of soil carbonate content and pH to avoid acidification risks; strongly-acid soils are potentially at aluminum toxicity risks and are required to raise soil pH to 5.5–6.5, an optimal pH range that ensures adequate nutrient supply for most crops. However, the soil with this range of pH is the most acid-sensitive, since soil exchangeable BCs is the main buffering substance. Decreasing the soil acidification rate and enhancing soil buffering capacity are then required in the stage.

Optimal N management can be regarded as the core of the mitigation strategies to maintain the optimal pH for crop production. The effective strategies include: (1) optimizing the N application rate, (2) managing N forms, (3) optimizing N transformation processes, and (4) integrated soil–crop system management. Optimizing N input based on crop demand can decrease nitrate losses via leaching, thereby reducing the loss of BCs. By adjusting N forms from ammonium-based to urea-based or nitrate-based, the acid production from nitrification of ammonium to nitrate can be significantly decreased; replacing synthetic fertilizer with organic fertilizers (crop residues, manure, and biochar) rich in BCs has the same effects and they also supplement soil BCs pool, enhancing soil buffering capacity. Also, use of nitrification inhibitors and urease inhibitors can decrease acidification from N transformations by minimizing N losses and increasing N use efficiency. The same effects occur with the integrated soil–crop system management by combining precision fertilizer application and optimal field management. Implementing these strategies can simultaneously decrease soil acidification and N losses, therefore optimizing crop production, minimizing environmental pollution, and promoting agricultural sustainability.

References

[1] Bardgett R D, van der Putten W H . Belowground biodiversity and ecosystem functioning. Nature, 2014, 515(7528): 505–511

[2] Kopittke P M, Minasny B, Pendall E, Rumpel C, McKenna B A . Healthy soil for healthy humans and a healthy planet. Critical Reviews in Environmental Science and Technology, 2024, 54(3): 210–211

[3] Wall D H, Six J . Give soils their due. Science, 2015, 347(6223): 695

[4] FAO and ITPS. Status of the world’s soil resources (SWSR)—Technical summary. Rome: FAO, 2015

[5] Sumner M E, Noble A D. Soil acidification: the world story. In: Rengel Z, ed. Handbook of Soil Acidity. New York: Marcel Dekker Inc., 2003, 1–28

[6] Ulrich B. An ecosystem approach to soil acidification. In: Ulrich B, Sumner M E, eds. Soil Acidity. Berlin: Springer Berlin Heidelberg, 1991, 28–79

[7] Kochian L V, Hoekenga O A, Pineros M A . How do crop plants tolerate acid soils? Mechanisms of aluminum tolerance and phosphorous efficiency. Annual Review of Plant Biology, 2004, 55(1): 459–493

[8] de Vries W, McLaughlin M J. Modeling the cadmium balance in Australian agricultural systems in view of potential impacts on food and water quality. Science of the Total Environment, 2013, 461−462: 240−257

[9] Mok J S, Yoo H D, Kim P H, Yoon H D, Park Y C, Lee T S, Kwon J Y, Son K T, Lee H J, Ha K S, Shim K B, Kim J H . Bioaccumulation of heavy metals in oysters from the southern coast of Korea: assessment of potential risk to human health. Bulletin of Environmental Contamination and Toxicology, 2015, 94(6): 749–755

[10] Msimbira L A, Smith D L . The roles of plant growth promoting microbes in enhancing plant tolerance to acidity and alkalinity stresses. Frontiers in Sustainable Food Systems, 2020, 4: 106

[11] Burt R. Soil Survey Field and Laboratory Methods Manual. Soil Survey Investigations Report No. 51, Version 2.0. Washington, D.C.: U.S. Department of Agriculture, Natural Resources Conservation Service, 2014

[12] Läuchli A, Grattan S R. Soil pH extremes. In: Shabala S, ed. Plant Stress Physiology. Wallingford: CABI International, 2012, 194–209

[13] Logan K A B, Floate M J S, Ironside A D . Determination of exchangeable acidity and exchangeable aluminium in hill soils part 1 exchangeable acidity. Communications in Soil Science and Plant Analysis, 1985, 16(3): 301–308

[14] Mc Lean E O. Soil pH and lime requirement. In: Page A L, ed. Methods of Soil Analysis: Part 2. Chemical and Microbiological Properties. 2nd ed. Madison: American Society of Agronomy, Soil Science Society of America, 1982, 199–224

[15] Weil R R, Brady N C. Soil acidity. In: Weil R R, Brady N C, eds. The Nature and Properties of Soils. 15th ed. Harlow: Pearson Education Limited, 2017, 392–437

[16] van Breenmen N, Mulder J, Driscoll C T . Acidification and alkalinization of soils. Plant and Soil, 1983, 75(3): 283–308

[17] Chadwick O A, Chorover J . The chemistry of pedogenic thresholds. Geoderma, 2001, 100(3−4): 321–353

[18] de Vries W, Breeuwsma A . Relative importance of natural and anthropogenic proton sources in soils in the Netherlands. Water, Air, and Soil Pollution, 1986, 28(1−2): 173–184

[19] Zhu Q, Liu X, Hao T, Zeng M, Shen J, Zhang F, De Vries W. Modeling soil acidification in typical Chinese cropping systems. Science of the Total Environment, 2018, 613−614: 1339−1348

[20] de Vries W, Posch M, Kämäri J . Simulation of the long-term soil response to acid deposition in various buffer ranges. Water, Air, and Soil Pollution, 1989, 48(3−4): 349–390

[21] Slessarev E W, Lin Y, Bingham N L, Johnson J E, Dai Y, Schimel J P, Chadwick O A . Water balance creates a threshold in soil pH at the global scale. Nature, 2016, 540(7634): 567–569

[22] Bolan N S, Hedley M J. Role of carbon, nitrogen, and sulfur cycles in soil acidification. In: Rengel Z, ed. Handbook of Soil Acidity. New York: Marcel Dekker Inc., 2003, 29–56

[23] Fujii K, Funakawa S, Hayakawa C, Kosaki T . Contribution of different proton sources to pedogenetic soil acidification in forested ecosystems in Japan. Geoderma, 2008, 144(3−4): 478–490

[24] Yu T R . Soil acidity characteristics and acidification problems in China. Chinese Journal of Soil Science, 1988, 20(2): 49–51

[25] Jiang J, Xu R, Zhao A . Surface chemical properties and pedogenesis of tropical soils derived from basalts with different ages in Hainan, China. Catena, 2011, 87(3): 334–340

[26] Reuss J O, Cosby B J, Wright R F . Chemical processes governing soil and water acidification. Nature, 1987, 329(6134): 27–32

[27] Blake L, Goulding K W T, Mott C J B, Johnston A E . Changes in soil chemistry accompanying acidification over more than 100 years under woodland and grass at Rothamsted Experimental Station, UK. European Journal of Soil Science, 1999, 50(3): 401–412

[28] Akselsson C, Hultberg H, Karlsson P E, Pihl Karlsson G, Hellsten S . Acidification trends in south Swedish forest soils 1986–2008—Slow recovery and high sensitivity to sea-salt episodes. Science of the Total Environment, 2013, 444: 271–287

[29] Lawrence G B, Hazlett P W, Fernandez I J, Ouimet R, Bailey S W, Shortle W C, Smith K T, Antidormi M R . Declining acidic deposition begins reversal of forest-soil acidification in the Northeastern U.S. and Eastern Canada. Environmental Science & Technology, 2015, 49(22): 13103–13111

[30] Yu Q, Zhang T, Ma X, Kang R, Mulder J, Larssen T, Duan L . Monitoring effect of SO₂ emission abatement on recovery of acidified soil and streamwater in southwest China. Environmental Science & Technology, 2017, 51(17): 9498–9506

[31] Chang C T, Yang C J, Huang K H, Huang J C, Lin T C. Changes of precipitation acidity related to sulfur and nitrogen deposition in forests across three continents in north hemisphere over last two decades. Science of the Total Environment, 2022, 806(Pt 1): 150552

[32] Guo J H, Liu X J, Zhang Y, Shen J L, Han W X, Zhang W F, Christie P, Goulding K W, Vitousek P M, Zhang F S . Significant acidification in major Chinese croplands. Science, 2010, 327(5968): 1008–1010

[33] Goulding K W T . Soil acidification and the importance of liming agricultural soils with particular reference to the United Kingdom. Soil Use and Management, 2016, 32(3): 390–399

[34] Johnston A E, Goulding K W T, Poulton P R . Soil acidification during more than 100 years under permanent grassland and woodland at Rothamsted. Soil Use and Management, 1986, 2(1): 3–10

[35] Tang C, Rengel Z. Role of plant cation/anion uptake ratio in soil acidification. In: Rengel Z, ed. Handbook of Soil Acidity. New York: Marcel Dekker Inc., 2003, 57–81

[36] Dong Y, Yang J L, Zhao X R, Yang S H, Mulder J, Dörsch P, Peng X H, Zhang G L . Soil acidification and loss of base cations in a subtropical agricultural watershed. Science of the Total Environment, 2022, 827: 154338

[37] de Vries W, Breeuwsma A . The relation between soil acidification and element cycling. Water, Air, and Soil Pollution, 1987, 35(3-4): 293–310

[38] Yan P, Shen C, Fan L, Li X, Zhang L, Zhang L, Han W . Tea planting affects soil acidification and nitrogen and phosphorus distribution in soil. Agriculture, Ecosystems & Environment, 2018, 254: 20–25

[39] Jin S Q, Zhang B, Wu B, Han D M, Hu Y, Ren C C, Zhang C Z, Wei X, Wu Y, Mol A P J, Reis S, Gu B J, Chen J . Decoupling livestock and crop production at the household level in China. Nature Sustainability, 2021, 4(1): 48–55

[40] Porter W M, McLay C D A, Dolling P J. Rates and sources of acidification in agricultural systems of southern Australia. In: Date R A, Grundon N J, Rayment G E, Probert M E, eds. Plant-soil Interactions at Low pH: Principles and Management. Developments in Plant and Soil Sciences, vol 64. Dordrecht: Springer, 1995, 75–83

[41] Tian D, Niu S . A global analysis of soil acidification caused by nitrogen addition. Environmental Research Letters, 2015, 10(2): 024019

[42] Yang X, Ni K, Shi Y, Yi X, Zhang Q, Fang L, Ma L, Ruan J . Effects of long-term nitrogen application on soil acidification and solution chemistry of a tea plantation in China. Agriculture, Ecosystems & Environment, 2018, 252: 74–82

[43] Chen D, Lan Z, Bai X, Grace J B, Bai Y . Evidence that acidification-induced declines in plant diversity and productivity are mediated by changes in below-ground communities and soil properties in a semi-arid steppe. Journal of Ecology, 2013, 101(5): 1322–1334

[44] Zhao X, Cai S, Xing G, Zhu Z. Nitrification and nitrogen leaching in tropical and subtropical acid soils. Soils, 2020, 52(1): 1−9 (in Chinese)

[45] Dong Y, Yang J L, Zhao X R, Yang S H, Mulder J, Dörsch P, Zhang G L . Seasonal dynamics of soil pH and N transformation as affected by N fertilization in subtropical China: an in situ ¹⁵N labeling study. Science of the Total Environment, 2022, 816: 151596

[46] Masud M M, Guo D, Li J, Xu R . Hydroxyl release by maize (Zea mays L.) roots under acidic conditions due to nitrate absorption and its potential to ameliorate an acidic Ultisol. Journal of Soils and Sediments, 2014, 14(5): 845–853

[47] Khonje D J, Varsa E C, Klubek B . The acidulation effects of nitrogenous fertilizers on selected chemical and microbiological properties of soil. Communications in Soil Science and Plant Analysis, 1989, 20(13−14): 1377–1395

[48] Yu Z, Chen H Y H, Searle E B, Sardans J, Ciais P, Peñuelas J, Huang Z . Whole soil acidification and base cation reduction across subtropical China. Geoderma, 2020, 361: 114107

[49] Cai Z, Wang B, Xu M, Zhang H, He X, Zhang L, Gao S . Intensified soil acidification from chemical N fertilization and prevention by manure in an 18-year field experiment in the red soil of southern China. Journal of Soils and Sediments, 2015, 15(2): 260–270

[50] Zhu Q, de Vries W, Liu X, Hao T, Zeng M, Shen J, Zhang F . Enhanced acidification in Chinese croplands as derived from element budgets in the period 1980–2010. Science of the Total Environment, 2018, 618: 1497–1505

[51] Zhang Q, Chu Y, Xue Y, Ying H, Chen X, Zhao Y, Ma W, Ma L, Zhang J, Yin Y, Cui Z . Outlook of China’s agriculture transforming from smallholder operation to sustainable production. Global Food Security, 2020, 26: 100444

[52] Pan X Y, Shi R Y, Hong Z N, Jiang J, He X, Xu R K, Qian W . Characteristics of crop straw-decayed products and their ameliorating effects on an acidic Ultisol. Archives of Agronomy and Soil Science, 2021, 67(12): 1708–1721

[53] Yuan J H, Xu R K, Qian W, Wang R H . Comparison of the ameliorating effects on an acidic Ultisol between four crop straws and their biochars. Journal of Soils and Sediments, 2011, 11(5): 741–750

[54] Hao T, Liu X, Zhu Q, Zeng M, Chen X, Yang L, Shen J, Shi X, Zhang F, de Vries W . Quantifying drivers of soil acidification in three Chinese cropping systems. Soil & Tillage Research, 2022, 215: 105230

[55] Cai Z, Yang C, Du X, Zhang L, Wen S, Yang Y . Parent material and altitude influence red soil acidification after converted rice paddy to upland in a hilly region of southern China. Journal of Soils and Sediments, 2023, 23(4): 1628–1640

[56] Helling C S, Chesters G, Corey R B . Contribution of organic matter and clay to soil cation-exchange capacity as affected by the pH of the saturating solution. Soil Science Society of America Journal, 1964, 28(4): 517–520

[57] Wen H Y, Wu H Y, Dong Y, Feng W J, Lu Y, Hu Y M, Zhang G L . Differential soil acidification caused by parent materials and land-use changes in the Pearl River Delta region. Soil Use and Management, 2023, 39(1): 329–341

[58] Araujo M A, Zinn Y L, Lal R . Soil parent material, texture and oxide contents have little effect on soil organic carbon retention in tropical highlands. Geoderma, 2017, 300: 1–10

[59] Xie J, Liang F, Liu Z, Jiang G, Zhang Q . Acidification characteristics and its influencing factors of red paddy soil derived from four parent materials in Southeast of China. Geoderma Regional, 2023, 34: e00673

[60] Meng C, Tian D, Zeng H, Li Z, Yi C, Niu S . Global soil acidification impacts on belowground processes. Environmental Research Letters, 2019, 14(7): 074003

[61] Raza S, Miao N, Wang P, Ju X, Chen Z, Zhou J, Kuzyakov Y . Dramatic loss of inorganic carbon by nitrogen-induced soil acidification in Chinese croplands. Global Change Biology, 2020, 26(6): 3738–3751

[62] Xiao H, Wang B, Lu S, Chen D, Wu Y, Zhu Y, Hu S, Bai Y . Soil acidification reduces the effects of short-term nutrient enrichment on plant and soil biota and their interactions in grasslands. Global Change Biology, 2020, 26(8): 4626–4637

[63] Fageria N K, Baligar V C. Chapter 7 Ameliorating soil acidity of tropical Oxisols by liming for sustainable crop production. In: Sparks D L, ed. Advances in Agronomy. Vol. 99. Academic Press, 2008, 345–399

[64] Cai Z, Wang B, Zhang L, Wen S, Xu M, Misselbrook T H, Carswell A M, Gao S . Striking a balance between N sources: mitigating soil acidification and accumulation of phosphorous and heavy metals from manure. Science of the Total Environment, 2021, 754: 142189

[65] Xie S, Yang F, Feng H, Yu Z, Liu C, Wei C, Liang T . Organic fertilizer reduced carbon and nitrogen in runoff and buffered soil acidification in tea plantations: evidence in nutrient contents and isotope fractionations. Science of the Total Environment, 2021, 762: 143059

[66] Shoghi Kalkhoran S, Pannell D J, Thamo T, White B, Polyakov M . Soil acidity, lime application, nitrogen fertility, and greenhouse gas emissions: optimizing their joint economic management. Agricultural Systems, 2019, 176: 102684

[67] Hijbeek R, van Loon M P, Ouaret W, Boekelo B, van Ittersum M K . Liming agricultural soils in Western Kenya: can long-term economic and environmental benefits pay off short term investments. Agricultural Systems, 2021, 190: 103095

[68] Rheinheimer D S, Tiecher T, Gonzatto R, Zafar M, Brunetto G . Residual effect of surface-applied lime on soil acidity properties in a long-term experiment under no-till in a Southern Brazilian sandy Ultisol. Geoderma, 2018, 313: 7–16

[69] Zuo W, Yi S, Gu B, Zhou Y, Qin T, Li Y, Shan Y, Gu C, Bai Y . Crop residue return and nitrogen fertilizer reduction alleviate soil acidification in China’s croplands. Land Degradation & Development, 2023, 34(11): 3144–3155

[70] Zhu Q, Liu X, Hao T, Zeng M, Shen J, Zhang F, de Vries W . Cropland acidification increases risk of yield losses and food insecurity in China. Environmental Pollution, 2020, 256: 113145

[71] Hao T, Zhu Q, Zeng M, Shen J, Shi X, Liu X, Zhang F, de Vries W . Impacts of nitrogen fertilizer type and application rate on soil acidification rate under a wheat–maize double cropping system. Journal of Environmental Management, 2020, 270: 110888

[72] Hao T, Zhu Q, Zeng M, Shen J, Shi X, Liu X, Zhang F, de Vries W . Quantification of the contribution of nitrogen fertilization and crop harvesting to soil acidification in a wheat–maize double cropping system. Plant and Soil, 2018, 434(1−2): 167–184

[73] Wang X, Xu M, Lin B, Bodirsky B L, Xuan J, Dietrich J P, Stevanović M, Bai Z, Ma L, Jin S, Fan S, Lotze-Campen H, Popp A . Reforming China’s fertilizer policies: implications for nitrogen pollution reduction and food security. Sustainability Science, 2023, 18(1): 407–420

[74] Yin Y, Zhao R, Yang Y, Meng Q, Ying H, Cassman K G, Cong W, Tian X, He K, Wang Y, Cui Z, Chen X, Zhang F . A steady-state N balance approach for sustainable smallholder farming. Proceedings of the National Academy of Sciences of the United States of America, 2021, 118(39): e2106576118

[75] Liu B, Wang X, Ma L, Chadwick D, Chen X . Combined applications of organic and synthetic nitrogen fertilizers for improving crop yield and reducing reactive nitrogen losses from China’s vegetable systems: a meta-analysis. Environmental Pollution, 2021, 269: 116143

[76] Wu L, Zhang W F, Cheng X P, Cui Z L, Fan M S, Chen Q, Zhang F S . Nitrogen fertilizer input and nitrogen use efficiency in Chinese farmland. Soil and Fertilizer Sciences, 2016, 4: 76–83

[77] Wang Z, Tao T, Wang H, Chen J, Small G E, Johnson D, Chen J, Zhang Y, Zhu Q, Zhang S, Song Y, Kattge J, Guo P, Sun X . Forms of nitrogen inputs regulate the intensity of soil acidification. Global Change Biology, 2023, 29(14): 4044–4055

[78] Weng Z, Butterly C R, Sale P, Li G, Tang C . Combined nitrate and phosphorus application promotes rhizosphere alkalization and nitrogen uptake by wheat but not canola in acid subsoils. Journal of Soils and Sediments, 2021, 21(9): 2995–3006

[79] Al-Harbi A R . Growth and nutrient composition of tomato and cucumber seedlings as affected by sodium chloride salinity and supplemental calcium. Journal of Plant Nutrition, 1995, 18(7): 1403–1416

[80] Anderson D S, Teyker R H, Rayburn A L . Nitrogen form effects on early corn root morphological and anatomical development. Journal of Plant Nutrition, 1991, 14(11): 1255–1266

[81] Cai A, Xu M, Wang B, Zhang W, Liang G, Hou E, Luo Y . Manure acts as a better fertilizer for increasing crop yields than synthetic fertilizer does by improving soil fertility. Soil & Tillage Research, 2019, 189: 168–175

[82] Shi R, Li J, Ni N, Xu R . Understanding the biochar’s role in ameliorating soil acidity. Journal of Integrative Agriculture, 2019, 18(7): 1508–1517

[83] Jiang J, Wang Y P, Yu M, Cao N, Yan J . Soil organic matter is important for acid buffering and reducing aluminum leaching from acidic forest soils. Chemical Geology, 2018, 501: 86–94

[84] Wang Z, Geng Y, Liang T . Optimization of reduced chemical fertilizer use in tea gardens based on the assessment of related environmental and economic benefits. Science of the Total Environment, 2020, 713: 136439

[85] Shi R Y, Ni N, Wang R H, Nkoh J N, Pan X Y, Dong G, Xu R K, Cui X M, Li J Y . Dissolved biochar fractions and solid biochar particles inhibit soil acidification induced by nitrification through different mechanisms. Science of the Total Environment, 2023, 874: 162464

[86] Elshayb O M, Nada A M, Farroh K Y, Al-Huqail A A, Aljabri M, Binothman N, Seleiman M F . Utilizing urea-chitosan nanohybrid for minimizing synthetic urea application and maximizing Oryza sativa L. productivity and N uptake. Agriculture, 2022, 12(7): 944

[87] Qiao C, Mia S, Wang Y, Hou J, Xu B . Assessing the effects of nitrification inhibitor DMPP on acidification and inorganic n leaching loss from tea (Camellia sinensis L.) cultivated soils with increasing urea-N rates. Sustainability, 2021, 13(2): 994

[88] Li J, Wang S, Luo J F, Zhang L L, Wu Z J, Lindsey S . Effects of biochar and 3,4-dimethylpyrazole phosphate (DMPP) on soil ammonia-oxidizing bacteria and nosZ-N₂O reducers in the mitigation of N₂O emissions from paddy soils. Journal of Soils and Sediments, 2021, 21(2): 1089–1098

[89] Ning J, Arai Y, Shen J, Wang R, Ai S . Effects of phosphorus on nitrification process in a fertile soil amended with urea. Agriculture, 2021, 11(6): 523

[90] Lan T, He X, Wang Q, Deng O, Zhou W, Luo L, Chen G, Zeng J, Yuan S, Zeng M, Xiao H, Gao X . Synergistic effects of biological nitrification inhibitor, urease inhibitor, and biochar on NH₃ volatilization, N leaching, and nitrogen use efficiency in a calcareous soil–wheat system. Applied Soil Ecology, 2022, 174: 104412

[91] Niu G, Wang R, Hasi M, Wang Y, Geng Q, Wang C, Jiang Y, Huang J . Availability of soil base cations and micronutrients along soil profile after 13-year nitrogen and water addition in a semi-arid grassland. Biogeochemistry, 2021, 152(2−3): 223–236

[92] Du C, Zhang L, Ma X, Lou X, Shan Y, Li H, Zhou R . A cotton high-efficiency water-fertilizer control system using wireless sensor network for precision agriculture. Processes, 2021, 9(10): 1693

[93] Nkebiwe P M, Weinmann M, Bar-Tal A, Müller T . Fertilizer placement to improve crop nutrient acquisition and yield: a review and meta-analysis. Field Crops Research, 2016, 196: 389–401

[94] Flynn K C, Spiegal S, Kleinman P J A, Meinen R J, Smith D R . Manureshed management to overcome longstanding nutrient imbalances in US agriculture. Resources, Conservation and Recycling, 2023, 188: 106632

Acknowledgements

This study was financially supported by Research and Development of Technical Approaches and Decision-making Systems for Precise Planting, Fertilization and Acid Control of Red Soil on Sloping Farmland project (2022YFD1900601), and Carbon Account Accounting and Emission Reduction and Carbon Sequestration Technology Research project (Qunonghe202231).

Compliance with ethics guidelines

Pengshun Wang, Donghao Xu, Prakash Lakshmanan, Yan Deng, Qichao Zhu, and Fusuo Zhang declare that they have no conflicts of interest or financial conflicts to disclose. This article does not contain any studies with human or animal subjects performed by any of the authors.

RIGHTS & PERMISSIONS

The Author(s) 2024. Published by Higher Education Press. This is an open access article under the CC BY license (http://creativecommons.org/licenses/by/4.0)