Contrasting Responses of N₂O Mitigation to Different Nitrification Inhibitors in Tea Plantation Soils

Abstract

Tea plantations are a hot-spot source of nitrous oxide (N₂O) emissions in the agricultural system. Using nitrification inhibitors (NIs) is a promising way to mitigate agricultural N₂O emissions and has been widely tested in many croplands. However, the efficiency of different NIs and whether there are soil-specific effects are still unclear in tea plantations with typical acidic soil conditions. This study evaluated the effects of three widely used NIs, i.e., dicyandiamide (DCD), 3,4-dimethylpyrazole phosphate (DMPP), and 2-chloro-6-(trichloromethyl) pyridine (Nitrapyrin), through a lab incubation trial, on the nitrification suppression, N₂O emissions, and ammonia-oxidizing microbial communities in two tea plantation soils with contrasting physicochemical properties (pH and texture). During the 50-day incubation, the soil with a higher pH and coarse texture (TA) exhibited a four-times-higher apparent nitrification ratio (ANR) than the more acidic and clay soil (HZ). Nitrification inhibitor addition resulted in about a 60% and 80% reduction in the ANR in HZ and TA soils, respectively. During the entire incubation, ammonium sulfate (N) addition without NIs emitted N₂O at 64.1 ± 1.2 and 61.5 ± 0.4 μg N kg⁻¹ (mean ± standard deviation, and the same in the following text) in the HZ and TA soils, respectively. Compared with the N alone, the N₂O mitigation efficiency of DCD, DMPP, and Nitrapyrin was 38.3% ± 0.4% (standard deviation), 33.8% ± 0.99%, and 36.5% ± 0.59% in the HZ soil and 94.1% ± 0.39%, 52.8% ± 1.05%, and 95.6% ± 0.65% in the TA soil, respectively. Nitrapyrin more effectively suppressed both ammonia-oxidizing archaeal (AOA) and ammonia-oxidizing bacterial (AOB) abundance, particularly in the acidic soil (HZ), where ammonia-oxidizing archaea dominate nitrification. These results revealed the pivotal role of soil properties in controlling NI efficiency and highlighted Nitrapyrin as a potential superior nitrification inhibitor for N₂O mitigation under the tested conditions in this study.

1. Introduction

Nitrous oxide (N₂O) is one of the key greenhouse gases (GHGs), contributing to global climate change. It has a 298-times-greater global warming potential (GWP) than carbon dioxide (CO₂) over 100 years [1]. Furthermore, N₂O is also the dominant ozone-depleting substance [2]. Soil N₂O emissions in agriculture contributed to about 60% of the total anthropogenic N₂O emissions [3]. More N₂O emissions will be emitted as the global population increases in the future [4]. Thus, finding effective mitigation strategies is still urgent and necessary in scientific research and policy making for agriculture.

Tea is the most consumed beverage after water and is widely cultivated in subtropical and tropical regions of Asia and Africa [5]. Despite a decline since the 1990s due to environmental concerns, the average annual nitrogen input in tea plantations remains exceptionally high, averaging 491 kg ha⁻¹ in China [6] and 600 kg ha⁻¹ in Japan [7]. These rates are 2.6 to 5.0 times those of cereal crops like rice, maize, and wheat [8]. Such intensive fertilization not only provides ample nutrients but also accelerates soil acidification [9], a condition known to favor N₂O production [10,11]. According to a systematic analysis in 2020 by Wang et al. [8], global tea plantations emit an estimated 57–84 Gg N₂O annually, accounting for 1.5–12.7% of the direct cropland N₂O emissions. These emissions contribute to global warming and reduce economic benefits by lowering nitrogen use efficiency (NUE). Therefore, mitigating N₂O losses in tea agroecosystems is essential for sustainable management.

The application of nitrification inhibitors (NIs) has been proposed as a promising way to reduce soil N₂O emissions in agriculture [12]. The most widely used NIs are dicyandiamide (DCD), 3,4-dimethylpyrazole phosphate (DMPP), and 2-chloro-6-(trichloromethyl) pyridine (Nitrapyrin) in the practice of improving nitrogen use efficiency [13,14]. However, the above three NIs have differences in longevity, mobility in soil, and efficiency in retarding the activity of ammonia-oxidizing microorganisms, due to their diverse chemical structures [15]. So far, most studies about NIs have been widely conducted in cereals and grasslands with semi-neutral or basic soil under a temperate climate; the efficiency of different NIs in tea plantations is still controversial [16,17]. The efficiency of NIs in reducing N₂O emission is also strongly dependent on soil conditions, e.g., soil texture and pH [18]. Tea plantation soil has exhibited a lower mitigation efficiency of DMPP than cropland soil, and its lower soil pH decreased the abundance and activity of AOB, the functional target of DMPP [19]. Furthermore, the shift in the AOA and AOB community structure after long-term tea plantation may alter NI effectiveness [20]. Therefore, testing different NIs across soils with contrasting properties is essential for evaluating their robustness.

In the present study, we conducted a controlled lab trial to evaluate the effects of three widely used nitrification inhibitors, DCD, DMPP, and Nitrapyrin, on N₂O emissions, nitrogen dynamics, and ammonia-oxidizing microbial communities in two contrasting tea plantation soils. The tested tea garden soils were collected from Hangzhou in Zhejiang (HZ) and Taian in Shandong (TA) as representative samples of China’s two primary tea plantation zones—the Jiangnan (south of Yangtze) and Jiangbei (north of Yangtze) tea plantation zones. The two soils typically represent the characteristic differences in soil pH and texture between southern and northern Chinese soils due to their pedogenic processes. We hypothesized that (1) NI performance would be higher in soils with a higher pH and loose texture, and (2) the three NIs would have a similar efficiency in identical soil due to the optimal application concentration.

2. Materials and Methods

2.1. Site Description

Soil samples were collected from tea plantations in Hangzhou (HZ) and Tai’an (TA), which belong to the Zhejiang and Shandong provinces, respectively, in China in 2019. Both have been planted with tea trees (Camellia sinensis) for green tea production.

The sampling site of HZ (120°05′ E, 30°10′ N) is located in a subtropical zone, has a monsoon climate. The soil at the sampling site is classified as Ultisol, developed from the parent material of a Quaternary eolian red deposit. The sampling site of TA (117°04′ E, 36°12′ N) is located in a temperate zone and also has a monsoon climate, but is drier and cooler than HZ. The soil in the site of TA is classified as Luvisols, developed from a parent material of granite weathering residual. More comparisons of soil properties are shown in

Table 1. Physio-chemical properties of the tested tea plantation soils for the incubation.

Properties	HZ	TA
Annual mean temperature (°C)	17.0	12.0
Annual total precipitation (mm)	1533	840
Soil taxonomy (USDA)	Ultisol	Luvisols
Soil texture (USDA)	Silty loam clay	Silt loam
Sand (%)	23.8	30.8
Silt (%)	53.1	67.9
Clay (%)	23.1	1.3
pH (%)	3.51	5.62
Total carbon (%)	2.7	1.6
Total nitrogen (%)	0.27	0.12
NH4+-N (mg kg−1)	41.2	28.1
NO3−-N (mg kg−1)	19.3	9.4
Available P (mg kg−1)	358	112
Available K (mg kg−1)	213	106

.

2.2. Soil Collection and Analysis

Before soil sampling, litter on the surface was removed. For each soil, composite soil samples (0–20 cm depth) were collected by a soil auger from multiple points across the tea plantation field. Fresh soil samples were transported on ice to the laboratory, where any visible stones, roots, and plant debris were manually removed. After that, soil samples were passed through a 2 mm sieve and stored at 4 °C for subsequent analyses and microcosm incubation.

Soil particle size distribution was determined using a laser diffraction particle size analyzer (Mastersizer 3000, Malvern Panalytical, Malvern, UK). Soil total C and N contents were determined using the elemental analyzer (Vario Macro Cube, Elementar, Langenselbold, Germany). Soil available P and K were extracted using Mehlich-3 reagent and determined using the Inductive Coupled Plasma Atomic Emission Spectrometer (iCAP 7400, Thermo Scientific, Waltham, MA, USA).

Soil pH was measured in a distilled water extraction (1/2.5 in w/v) using a soil pH electrode (Orion 3 Star, Thermo, USA). Soil NH₄⁺-N and NO₃⁻-N in the fresh soil samples were extracted with 1 M KCl (Sinopharm Chemical Reagent Co. Ltd., Shanghai, China) with a soil:solution by 1:10 (w/v) and then determined using the Automatic Chemistry Analyzer (SmartChem 140, AMS Alliance, Frépillon, France).

2.3. Experiment Design

The lab incubation included five treatments: background without any nitrogen or nitrification inhibitor (CK), chemical nitrogen addition alone (N), N plus DCD (10% of added N, DCD, Sanpu Chemical Co., Ltd., Shanghai, China), N plus DMPP (1% of added N, DMPP, J&K Scientific Co., Ltd., Shanghai, China), and N plus Nitrapyrin (1% of added N, Nitrapyrin, Aofuto Chemical Co., Ltd., Shanghai, China). To ensure the substrate saturation for N₂O detection in the incubation vial, nitrogen was added at a rate of 500 mg kg⁻¹ (based on dry soil weight) as a (NH₄)₂SO₄ (Sinopharm Chemical Reagent Co., Ltd., Shanghai, China) solution, corresponding to a field application rate of 1000 kg N ha⁻¹. This amount was about 100% and 20% higher than the average amount in the tea plantation of HZ (467 kg N ha⁻¹) and TA (792 kg N ha⁻¹).

For the incubation, 20 g of soil (fresh soil but based on the oven dry weight) was placed into a glass jar (250 mL in volume, 10 cm in height), and then distilled water was added to reach a soil moisture of 60% maximum water hold capacity (WHC). To stabilize microbial activity following soil disturbance during the sampling, transportation, and storage, all soil samples in the jars were pre-incubated under the aerobic incubation condition at 25 °C with 60% WHC for 2 days in the climate chamber before the treatment. After the pre-incubation, all chemicals were evenly added as a solution to the soil surface and then mixed. During the incubation, the jars were kept open in the climate chamber, and the soil moisture (60% WHC) was maintained through the daily addition of distilled water according to the weight change.

Each treatment was replicated in 28 jars, and 280 jars in total were used simultaneously in this study. To minimize the interference of potentially uneven temperature and humidity in the climate chamber, all jars were put on four layers from the top to the bottom with the same amount and randomly selected from each layer during each sampling.

During the sampling, four fixed jars were selected in each treatment for gas measurement during the whole incubation period. Moreover, four replicates of each treatment were randomly taken out from the climate chamber for soil analysis on days 1, 7, 14, 25, 36, and 50 after the treatment. About 5 g of sampled fresh soil was immediately frozen in the fridge at −20 °C for soil DNA extraction. The left soils were kept at 4 °C for analyses of pH and the concentrations of NH₄⁺-N and NO₃⁻-N.

2.4. Soil Gas Sampling and N₂O Concentration Determination

The N₂O emission was measured through a semi-static chamber method. Before the experiment, all incubation jars should pass the blank test with pre-evacuated jars. After 2 h, the airtightness was measured according to the status of whether the pressure in the jars significantly increased using an electronical manometer (PG-100-102GP, COPAL ELECTRONICS, Kyoto, Japan).

Gas samples were collected at 1, 3, 6, 10, 15, 21, 28, 35, 45, and 50 days after the treatment. The static closed chamber method was conducted to measure the N₂O emission for the advantage of high sensitivity. Before the gas sampling, the jars for gas sampling were sealed with a rubber stopper and silicone gel, and then the air in the sealed jars was evacuated for one minute with a vacuum pump. After that, the ambient air was introduced into the sealed jar to keep all jars at the same start concentration. This evacuation and air replacement was repeated three times to ensure the jar was fully filled with fresh air. During the final air introduction, a 15 mL gas sample was collected into a pre-vacuumed glass vial (738W, Labco, Lampeter, UK) and marked as the initial sample. After 6 h, a 15 mL gas sample was taken using a gas-tight syringe and was marked as the final sample. Before final gas sampling, the air in the sealed jar was evenly mixed using a syringe to ensure homogeneity. After gas sampling, the sealed jar was evacuated, and fresh air was introduced. The rubber stopper was also removed to keep the aerobic condition for further incubation.

The N₂O concentration in the collected gas samples was determined using a gas chromatograph (GC 7890B, Agilent, Santa Clara, CA, USA). The air in the vials was pumped into the GC with a robotic sampler (CA-6, Jiangbo, Beijing, China). The sampled air passed through the GC, with pure N₂ (99.999%) as a carrier gas at a flow rate of 30 mL min⁻¹. Different gas components were separated by a stainless-steel column packed with Porapak Q (80/100 mesh) at 55 °C. The N₂O signal intensity was determined using the electron capture detector (ECD) at 300 °C. The N₂O concentration in the gas sample was linearly scaled to the pre-mixed reference gas with a known N₂O concentration. For quality check, the GC was calibrated daily using a multi-point calibration curve with certified standard gases at five different N₂O concentrations (350 ppbv, 450 ppbv, 600 ppbv, 750 ppbv, and 900 ppbv). During the sample measurement, a standard (N₂O 450 ppbv) was analyzed after every 12 samples to correct for ECD drift.

2.5. Ammonia-Oxidizing Gene Abundance

Soil DNA was extracted from 0.25 g soil samples taken on day 1, 14, and 50 with the soil DNA extraction kit (FastDNA Spin Kit for Soil, MP Bio, Santa Ana, CA, USA) according to the product protocol. The final DNA concentration was determined using a UV–VIS spectrophotometer (NanoDrop 2000, Thermo Scientific, Waltham, MA, USA), and the DNA quality was checked through 1% agarose gel electrophoresis. The extracted DNA samples were stored at −20 °C for further analysis.

The microbial population involved in ammonia-oxidizing was assessed by quantifying the amoA gene copies of AOA, AOB, and TAO100, respectively, which were determined through real-time quantitative PCR (qPCR) under specific primers and conditions. The paired primers were Arch-amoA23F/Arch-amoA616R [21], amoA-F/amoA-R [22], and TAO-amoAF/TAO-amoAR [23] for AOA, AOB, and TAO100, respectively. The reaction mixture (20 μL) contained 2.0 μL soil DNA extract, 10.0 μL ready-to-use SYBR Green qPCR Super-Mix UDG with Rox (Invitrogen, Thermo Fisher, Waltham, MA, USA), 0.4 μL forward primers (10 μM), 0.4 μL reverse primers (10 μM), and 7.2 μL DNA-free water.

Primer specificity was confirmed through melting curve analysis and gel electrophoresis. Each qPCR was performed in triplicate using a standard curve and a negative control. Plasmids containing the cloned AOA-amoA, AOB-amoA, and TAO100-amoA genes were used for establishing the standard curve. The reaction efficiencies ranged from 97% to 104%, and the R² values ranged from 0.990 to 0.999 for all three amoA genes.

For convenient comparison, the obtained raw gene copies per reaction were scaled to absolute gene copies per gram of dry soil according to the DNA dilution factor and the dry mass of the soil sample used for DNA extraction.

2.6. Calculation and Statistical Analysis

The N₂O emission rate was calculated as follows [15]:

$$F ={\displaystyle \frac{\rho \times \delta C\times V}{\delta t\times W}}\times {\displaystyle \frac{273.15}{273.15+T}}\times {10}^{-3}$$

(1)

where F was the emission rate (μg N kg⁻¹ d⁻¹), ρ was the N₂O-N density (1.25 kg m⁻³) at the standard condition, δC was the N₂O concentration change (ppbv) during the closure period, δt was the seal duration (0.25 day), V was the headspace volume of the incubation jar (0.25 L), W was the dry soil weight (0.02 kg), and T was the incubation temperature (25 °C). The headspace volume of the incubation jars (V) was also corrected for the volume occupied by the incubated soil (~7.5 mL), which was calculated using the dry mass and approximate bulk density.

The cumulative soil N₂O emission was calculated through linear integration as follows [15]:

$$Cumloss =\sum _{i =1}^n\left({\displaystyle \frac{F_i+F_{i+1}}{2}}\right)\times \left(t_{i+1}-t_i\right)$$

(2)

where Cumloss is the cumulative N₂O emission (μg N kg⁻¹), F_i is the N₂O emission rate of the ith measurement (μg N kg⁻¹ d⁻¹), i represents the sampling sequence from 1 to 10, t represents the sampling date, and the difference in the adjacent sampling dates (t_i+1 − t_i) represents the sampling interval (days) from 2 to 15.

The apparent nitrification ratio (ANR, %) was calculated as the relative contribution of nitrate in the total mineral N concentration [24]:

$$ANR ={\displaystyle \frac{{NO}_3^{-}}{{NH}_4^{+}+{NO}_3^{-}}}\times 100$$

(3)

The nitrification inhibition efficiency (NIE) was calculated as follows [24]:

$$NIE\left(\mathrm{\%}\right)=(1-{\displaystyle \frac{{ANR}_i}{{ANR}_c}})\times 100$$

(4)

where ANR_c and ANR_i were the net nitrification rate with and without nitrification inhibitor addition, respectively.

To compare the overall treatment effect on dynamic soil characteristics, e.g., pH, chemical N, and amoA gene abundance, the trapezoid averaged values (AVE) were calculated instead of the simple algorithm average as follows [9]:

$$AVE ={\displaystyle \frac{AUC}{t}}$$

(5)

where AVE was the trapezoid averaged values with the same unit of the raw variable, AUC was the area under the dynamic change curve, which could be calculated according to the trapezoid area rule, and t was the incubation duration (50 days).

The effects of soil, treatment, and sampling date on the soil N₂O emission rate and soil properties were tested using three-way ANOVA with interaction effects. In the ANOVA for soil N₂O emission rate, soil and treatment were between-group factors, while the sampling date was set as a within-group factor, since the gas samples were taken from the fixed jars during the whole incubation. Alternatively, the sampling date was set as the between-group factor in the ANOVA for soil properties, since soil samples were taken from randomly selected jars.

The effects of soil and treatment on the cumulative N₂O emission, as well as the trapezoid averaged values of soil properties, nitrification rate, and nitrification inhibition efficiency, were tested using two-way ANOVA. If the interaction effect was significant, the post hoc comparison between pairwise groups was carried out using the Turkey method for each soil. The effect size was assessed using the index partial eta square (partial η²). The relationships between the trapezoid averaged values of soil properties and cumulative N₂O emissions were tested through Pearson correlation analysis. Path modeling with a partial least square algorithm (PLS-PM) was carried out to demonstrate the casual relationships among the observed and latent variables. The overall model performance was assessed with the Goodness-of-Fit index, which accounts for the overall quality at both the measurement and the structural models. In the path model, the strength and direction of the direct effects were represented by the path coefficients between structural variables, while the indirect effects were represented by the sum of the products of all possible path coefficients except the direct effect. All above calculations and statistical analyses were performed on the platform R (version 4.3.0). The contribution package ‘plspm’ (version 0.6.0) was used for path modeling [25].

3. Results

3.1. Soil NH₄⁺-N, NO₃⁻-N, and pH

Both the soil and treatment significantly influenced soil NH₄⁺-N, NO₃⁻-N, and pH changes during the incubation (Table S1). Generally, soil NH₄⁺-N concentrations gradually decreased and remained relatively stable after day 25 (Figure 1). However, TA soil exhibited a more rapid decline than HZ soil. Compared with N alone, the NI addition maintained more NH₄⁺-N throughout the incubation. At the end of the incubation, Nitrapyrin exhibited the highest NH₄⁺-N concentration in both soils, while DCD and DMPP retained less in the HZ and TA soils, respectively. The overall soil NH₄⁺-N concentrations were also significantly affected by the soil and the treatment (Table S2). HZ soil could retain more NH₄⁺-N than the TA soil after the N addition (Figure S1). Three NIs exhibited a significantly higher overall soil NH₄⁺-N concentration than the N alone. However, DMPP showed a lower soil NH₄⁺-N concentration than the other two NIs in the TA soil, which was not found in the HZ soil.

Generally, the soil NO₃⁻-N concentration increased with time, and its dynamic was also significantly influenced by the soil, treatment, and sampling time (Table S1). Nitrogen addition without NIs (N) maintained more NO₃⁻-N than CK, and the TA soil exhibited a significantly more rapid increase in the soil NO₃⁻-N concentration than the HZ soil (Figure 1). At the end of incubation, the HZ and TA soils accumulated about 75 and 270 mg kg⁻¹ in the treatment with N alone. NI addition significantly retarded the soil NO₃⁻-N accumulation and exhibited lower soil NO₃⁻-N concentrations than N alone. Among the three NIs, Nitrapyrin exhibited the lowest NO₃⁻-N concentration, while DCD and DMPP accumulated the most NO₃⁻-N in the HZ and TA soils, respectively, at the end of incubation. The overall trapezoid averaged NO₃⁻-N concentration was also significantly different for soils and treatments (Table S2), and Nitrapyrin maintained the least NO₃⁻-N among all treatments (Figure S1).

The soil, treatment, and sampling time still significantly influenced the soil pH dynamics (Table S1). In both soils, the soil pH decreased after nitrogen alone, while it firstly increased with NI addition. Soil pH varied between 3.15 and 3.49 in the HZ soil, while it exhibited a much larger variation with a range of 3.25~5.25 in the TA soil (Figure 1). In the TA soil, treatments with NIs showed a hump-shape change, which was not obvious in the HZ soil. Furthermore, the final soil pH values in the TA soil were all lower than the initial value. The overall soil pH value was significantly different among treatments depending on the soil (Table S2). In the HZ soil, the overall pH difference was small, while DCD and N alone showed the highest and lowest overall soil pH in the TA soil (Figure S1).

3.2. Apparent Nitrification Ratio and Nitrification Inhibition Efficiency

During the incubation, the apparent nitrification ratio (ANR) increased in both soils, with a more pronounced rise observed in the TA soil (Figure S2). The addition of nitrification inhibitors (NIs) resulted in a lower ANR compared to the N alone treatment, particularly in the TA soil. The overall ANR under the N alone treatment reached 12% in the HZ soil (Figure 2), while three NI additions reduced the overall ANR to 3.6%~4.4%, though the differences among them were not significant. In contrast, in the TA soil, these NIs significantly reduced the overall ANR to 8.8–18%, and Nitrapyrin resulted in largest reduction compared with the other two NIs.

The nitrification inhibition efficiency (NIE) ranged from 50% to 75% in the HZ soil and from 20% to 88% in the TA soil. The initial NIE in the TA soil was approximately 50% lower than that in the HZ soil (Figure S2). However, the NIE in the TA soil increased rapidly, peaking at around 80% by day 25. The statistical analysis indicated that, while the soil type did not exert a significant simple effect on NIE, the treatment factor had a significant influence (Table S4).

The overall NIE was significantly affected by the interaction between soil type and treatment (Table S4). In both soils, Nitrapyrin showed the significantly highest overall NIE (64% in HZ and 71% in TA), whereas DCD and DMPP exhibited the lowest NIE by 59% in the HZ soil and 58% in the TA soil, respectively (Figure 2).

3.3. Soil N₂O Emission

The soil N₂O emission change was significantly influenced by the soil and treatment, with interactions (Table S5). In the HZ soil, CK showed a stable and low N₂O emission rate, ranging between 0.65 and 1.13 μg N kg⁻¹ d⁻¹ (Figure 3A). Nitrogen addition alone showed higher emission rates than CK in the first week but decreased and became lower than CK after day 10, except in the treatment with N alone. The N₂O emission rate in the treatment with N alone showed an increase after day 20, while all NI treatments maintained a decreasing trend.

In the TA soil, N₂O emission rates were generally lower than those in the HZ soil, except for the N alone (Figure 3B). Furthermore, the emission rate in N alone firstly kept increasing to a peak of 2.8 μg N kg⁻¹ d⁻¹ until day 15 and then decreased. Compared with the treatment with N alone, NI additions exhibited lower N₂O emission rates and a decreasing pattern at the beginning. DMPP showed higher N₂O emission rates than the other two NIs. Furthermore, the emission rate in DMPP began to increase on day 10 and reached a peak of 0.8 μg N kg⁻¹ d⁻¹ on day 35. Throughout the whole incubation, the N₂O emission rates in treatments DCD and Nitrapyrin were relative stable, but lower than 0.2 μg N kg⁻¹ d⁻¹.

The cumulative N₂O emission was largely affected by the soil and treatment, with a significant interaction effect (Table S6). In the HZ soil, the background cumulative N₂O emissions (CK) were 47.2 μg N kg⁻¹, while the N addition alone (N) resulted in a 36% increase ober CK to 64.1 μg N kg⁻¹ (Figure 3C). Compared to N alone, DCD showed the largest reduction, by 38%, but there was no big difference between DCD and DMPP or Nitrapyrin, which also showed about a 35% reduction.

The cumulative N₂O emissions in the TA soil were lower than those in the HZ soil (Figure 3D). The highest cumulative N₂O emission in the TA soil was also observed in the treatment with N alone, at 61.5 μg N kg⁻¹, which was 266% more than that of CK, which emitted 16.8 μg N kg⁻¹ during the 50-day incubation. Compared with N alone, NI additions exhibited a significant reduction, by 53–95%, and DCD and Nitrapyrin showed a larger reduction than DMPP.

3.4. Abundances of amoA Genes

During the incubation, the change in the soil AOA, AOB, and TAO100 abundance was significantly influenced by the soil, treatment, and incubation time (Table S7). Both soils showed similar initial AOA amoA gene abundances, but exhibited a descending trend in the HZ soil and a hump-shape in the TA soil, respectively (Figure S3). Compared with N alone, DMPP and DCD exhibited significantly lower AOA abundances in the HZ and TA soils, respectively. At the end of incubation on day 50, the AOA abundance was significantly lower in all NIs in HZ soil, but only significantly lower in DMPP in the TA soil (Figure S3). The initial gene abundances of AOB amoA were much lower than those of AOA in both soils. All treatments exhibited an increasing AOB abundance in the HZ soil, while there was no significant difference in the TA soil, except with N alone (Figure S3). Compared with N alone, NI additions exhibited a decrease in AOB abundance, which was larger in the TA soil. At the end of incubation, DMPP showed the significantly lowest AOB amoA gene abundance among NIs in the HZ soil. The initial TAO100 amoA gene abundance did not show any difference among treatments in both soils on day 1 (Figure S3). Meanwhile, at the end of incubation, nitrogen alone (N) exhibited a significantly higher TAO100 abundance than CK in HZ soil. Compared with N alone, only Nitrapyrin among the three NIs significantly reduced the TAO100 abundance at the end of incubation.

The overall AOA, AOB, and TAO100 gene abundance was significantly affected by the interactions between soils and treatments according to the results of the two-way ANOVA (Table S8). In the HZ soil, the N treatment showed the highest overall AOA abundance, which was significantly reduced by Nitrapyrin, and further significantly reduced by both DCD and DMPP. A different pattern was found in the TA soil, where the N and DMPP treatments maintained similarly high AOA abundances, both significantly exceeding the statistically indistinguishable levels in DCD and Nitrapyrin (Figure 4). The response of the average AOB abundance to the NIs also differed between soils. In the HZ soil, while the N treatment yielded the highest AOB, Nitrapyrin and DCD showed an intermediate and comparable suppressive effect, both being significantly higher than DMPP. In the TA soil, the N alone treatment also resulted in a significantly higher AOB abundance than all NIs, which did not differ significantly from each other. The two-way ANOVA also confirmed that the overall TAO100 amoA gene abundance was significantly affected by the interaction of soil and treatment (Table S8). Its abundance in the HZ soil was resilient to all treatments, showing no significant differences. In the TA soil, a significant suppression was evident under DCD and Nitrapyrin, as abundances in the N and DMPP treatments were comparable and significantly larger.

3.5. Structural Path Model

The N₂O emission rates were significantly correlated with the soil NH₄⁺-N, pH, and amoA gene abundance of AOA, AOB, and TAO100 (Figure S4). The cumulative N₂O emission showed significantly positive correlations with soil NO₃⁻-N, but a negative correlation with soil NH₄⁺-N and pH. Furthermore, the cumulative N₂O emission was significantly correlated with only AOA abundance in the HZ soil (Figure 5A), but with all three amoA gene abundances in the TA soil (Figure 5B). The soil NH₄⁺-N exhibited a significantly negative correlation with soil NO₃⁻-N, but a positive correlation with pH in both soils. The soil NO₃⁻-N had a significantly negative correlation with AOA in the HZ soil, but a positive correlation with AOB expression in the TA soil. The soil pH exhibited a positive correlation with the amoA gene abundance, only with AOA in the HZ soil but with all three in the TA soil. Among the three amoA gene abundances, AOA only exhibited a positive correlation with AOB in the HZ soil, and only had positive correlation with TAO100 in the TA soil. There was no significant correlation between AOB and TAO100 in both soils.

The partial least squares path model (PLS-PM) integrated environmental, chemical, and microbial drivers for N₂O emissions. The inner (structural) model explained more than 80% of the variance for each inner variable, and four inner variables accounted for 97% of the variance of the cumulative N₂O emissions (Figure 6A). The overall model prediction power (GoF) was 0.74. Soil NH₄⁺-N and NO₃⁻-N exhibited significantly direct relationships with N₂O emissions, while pH and ammonia-oxidizing gene abundance (AOM) exhibited negative path coefficients. Both soil and NH₄⁺-N showed positive path coefficients with AOM, while pH did not. The factor for soil had a negative path relationship with NH₄⁺-N, which was also negatively correlated with NO₃⁻-N. In the outer model, the sampling site (Site) contributed more than nitrification inhibitor (NI) to the factor for soil, while AOB abundance contributed most to the variation in the factor for AOB.

Among the factors influencing N₂O emission, soil NH₄⁺-N and pH are the two main inner variables influencing the total effect (Figure 6B). In the direct pathways, soil NO₃⁻-N and pH exhibited the greatest positive and negative effects, respectively. Meanwhile, in the indirect effects, all inner variables contributed negatively to the N₂O emission, and NH₄⁺-N and AOM were the two largest contributors. AOM showed significant positively direct, but negatively indirect, effects on the N₂O emissions. Although the treatment of the soil (combination of site and NIs) contributed the smallest effect to N₂O emissions, it showed the strongest total effect on the AOM, which was mostly from the direct pathway. Moreover, soil NH₄⁺-N contributed a secondary impact to AOM, while pH showed the weakest influence. Most NO₃⁻-N variations were directly from NH₄⁺-N, which also showed a significant indirect effect mediated via AOM.

4. Discussion

4.1. Effects of Soil Properties on Nitrification Inhibition Efficiency

The dynamics of soil NH₄⁺ and NO₃⁻ were strongly affected by the soils and nitrification inhibitors (Table S1). Despite the addition of nitrification inhibitors, the TA soil showed a faster decline of soil NH₄⁺ concentration (Figure 1) and a higher apparent nitrification ratio than the HZ soil (Figure 2). These results indicated the higher baseline nitrification activity of TA soil, which means more favorable conditions for nitrification organisms in the TA soil.

The dependence of nitrification activity on soil properties, e.g., pH, organic carbon, and texture, has also been reported in previous studies [26,27,28]. The higher pH and porous texture in the TA soil may be the pivotal factors contributing to the difference in the apparent nitrification ratio, since nitrifier activity is strongly constrained under acidic conditions, and the relatively higher pH in the TA soil may have a faster nitrification rate [29,30]. From a physiological perspective, the higher pH and more porous texture in the TA soil can create favorable conditions for supplying more substates for nitrification, since there is a pH-dependent equilibrium between the ammonia and ammonium [31], and the higher porosity indicates more O₂ supply for aerobic nitrification.

All three NIs showed significant effects in suppressing NH₄⁺ depletion and NO₃⁻ accumulation, but their performance was significantly different between soils (Figure 1). Nitrapyrin exhibited the lowest apparent nitrification ratio and strongest inhibition efficiency in both soils (Figure 2). However, DCD and DMPP showed a soil-specific effect in the nitrification inhibition efficiency, with a significant difference in TA soils (Figure 2). To clarify these soil-specific responses, the inherent properties of the HZ soil should be considered. The lack of significant differences among the three NIs in the HZ soil can be attributed to its inherently low baseline nitrification activity, which was likely constrained by the low soil pH (Table 1). Beyond pH, the finer texture and higher soil organic carbon (SOC) content in the HZ soil may also further reduce NI efficiency. Specifically, soils with higher clay and organic matter content are known to strongly adsorb organic compounds, potentially reducing the bioavailability of NIs like DCD and DMPP [32]. Furthermore, a higher SOC content can support a more active and diverse microbial community, potentially accelerating the biodegradation of these inhibitors [18,32]. This attenuated effect of NIs in soils with a low intrinsic nitrification potential has also been documented in other studies [33]. The divergent responses in the two soils clearly demonstrate that NI effectiveness is not universal but is strongly controlled by soil properties. Our results implied that factors like clay content and SOC, which influence inhibitor sorption and persistence, are critical determinants of NI performance. This soil-specific interaction highlights the necessity of considering the inherent soil characteristics when selecting and evaluating NIs for practical applications.

4.2. Efficiency of N₂O Mitigation by NIs in Contrasting Soils

Cumulative N₂O emissions differed significantly between soils and treatments, reflecting variations in the mitigation potential of NIs (Table S6). Overall, emissions were substantially higher in the HZ soil than in the TA soil (Figure 3), consistent with its higher SOC content and lower pH [34,35,36,37]. Although the TA soil exhibited a faster nitrification and greater NO₃⁻ accumulation (Figure 1 and Figure 2), its lower N₂O emissions suggest that nitrification-derived N₂O was less important here, or that the reduction of N₂O to N₂ was more efficient. This aligns with studies identifying denitrification as the dominant N₂O source in tea soils [38].

The elevated emissions in the acidic HZ soil are likely due to the low pH simultaneously impairing N₂O consumption and promoting its production. Acidic conditions strongly inhibit N₂O reductase (NosZ), hindering the reduction of N₂O to N₂ during heterotrophic denitrification [35]. Concurrently, nitrifier denitrification by ammonia-oxidizing bacteria (AOB) is often enhanced at a low pH, as they adapt by upregulating nitric oxide reductase (NorB), leading to N₂O accumulation [39,40]. Thus, the high N₂O emissions from HZ soil likely result from both impaired N₂O consumption and a significant contribution from AOB-driven nitrifier denitrification, a pathway whose importance increases as soil pH declines [41].

Chemical N addition alone increased N₂O emissions in both soils, but the stimulatory effect was significantly stronger in the TA soil, whereas emissions in the HZ soil increased by only 18% (Figure 3). This disparity reflected contrasting balances between nitrification and denitrification processes, which are strongly influenced by soil texture, aeration, and pH [42,43]. In the TA soil, nitrogen addition provided a more abundant substrate for N₂O production, as environmental constraints such as pH and texture were less limiting. Nitrification inhibitors substantially suppressed N₂O fluxes in both soils, though their mitigation efficiencies differed. In the HZ soil, the N₂O mitigation efficacy of NIs varied between 35% and 38%, with the order of DCD > Nitrapyrin > DMPP. In the TA soil, the order was Nitrapyrin > DCD > DMPP, with DMPP being substantially less effective. Both Nitrapyrin and DCD reduced cumulative emissions by more than 90%, whereas DMPP showed a markedly weaker mitigation (Figure 3). This pattern aligns with the observed soil NO₃⁻ dynamics (Figure 1) and overall nitrification inhibition efficiency (Figure 2), where DMPP was less effective at retaining soil NO₃⁻ and exhibited a lower inhibition in the TA soil.

The soil-dependent efficacy of nitrification inhibitors (NIs) is closely tied to their ability to regulate substrate availability for microbial N₂O production. Nitrapyrin, which consistently and strongly inhibited nitrification, achieved the most stable N₂O reduction across both soils, which was also supported in previous studies [12,13]. Its superior performance may be attributed to a higher hydrophobicity and stronger resistance to microbial degradation, particularly under acidic conditions [41,42]. By contrast, DMPP showed a lower efficiency than DCD in the TA soil, a result that appears inconsistent with reports of DMPP’s typically longer persistence and stronger efficacy [12,43]. This discrepancy may be due to the specific conditions of the TA soil requiring a higher functional concentration of DMPP for effective inhibition. Key soil factors such as low pH and a nitrifier community potentially dominated by ammonia-oxidizing archaea (AOA) can reduce DMPP’s bioavailability or require a higher threshold for inhibition, as DMPP primarily targets AOB [19]. A previous study noted that DMPP’s effective concentration can be 2–5 times higher than other NIs in some soils [44], implying that our DMPP dose may be insufficient. The observed higher abundance of ammonia oxidizers under DMPP treatment (Figure 4) confirmed that the inhibition was incomplete.

4.3. Ammonia-Oxidizing Microbes Driving N₂O Emission

The abundance of ammonia-oxidizing microorganisms (AOMs) provided further insight into the mechanisms underlying N₂O mitigation by nitrification inhibitors (NIs). In contrast to studies conducted in neutral croplands, the AOM community in these acidic tea soils was dominated by AOA and TAO100, whereas AOB abundance remained relatively low (Figure 4). This pattern aligns with previous reports indicating the numerical dominance of AOA and TAO100 under strongly acidic conditions, where AOB are often suppressed [45,46]. Nitrogen fertilization (N) stimulated AOB in both soils but exerted divergent effects on AOA. It significantly increased AOA abundance in the HZ soil but decreased it in the TA soil. This may reflect the more favorable pH in the TA soil, enabling AOB to temporarily outcompete AOA following the initial NH₄⁺ pulse, as supported by the marked increase in AOB after N addition in this soil (Figure S3).

The application of NIs further modulated the composition of the AOM community. In the HZ soil, all three inhibitors effectively suppressed AOA abundance relative to the N only treatment, whereas, in the TA soil, their primary effect was observed on AOB (Figure 4). This suggested a potential shift in the dominant ammonia-oxidizing populations between soils, which may influence NI efficacy. In the HZ soil, the reduction in AOA abundance under NI treatments was consistent with the observed decline in cumulative N₂O emissions (Figure 5), implying a possible link between AOA activity and N₂O production in this acidic soil. By contrast, in the TA soil, AOA abundance was less responsive to NIs, particularly DMPP, suggesting a comparatively smaller role of AOA in N₂O generation under less acidic conditions. AOB abundance increased over time in the HZ soil (Figure S3) but remained low across most treatments in the TA soil. Interestingly, TAO100 abundance was significantly reduced only by Nitrapyrin in both soils (Figure S3), suggesting a broader inhibitory scope of this compound across different ammonia oxidizer groups.

In the HZ soil, cumulative N₂O emissions were only significantly correlated with AOA abundance (Figure 5), underlining the dominant contribution of AOA in the acidic soils. By contrast, in the TA soil, N₂O emissions were correlated with all three AOM groups, indicating that multiple AOMs jointly contributed to N₂O production (Figure 5). This soil-dependent partitioning of microbial contributions is consistent with previous findings that AOA dominate under acidic or low N conditions, while AOB prevail under a higher N availability and neutral pH [34,45,47]. Considering most tea plantation soils have a pH less than 5.5, AOA would play a pivotal role in N transformation after fertilization [20].

According to the effect size of different factors in the pathway model (Figure 6B), soil NH₄⁺-N (effect = 0.96) and NO₃⁻-N (effect = 0.59) exerted significant positive direct effects on N₂O emissions, whereas pH showed a strong negative direct influence (effect = −0.74). In contrast, the ammonia-oxidizing microorganism (AOM) abundance exhibited a dual role, with a positive direct effect (effect = 0.39) on N₂O, while a stronger overall negative indirect effect (effect = 0.72) was mediated through substrate consumption and pathway regulation. Nitrification inhibitors (NIs) reduced N₂O emissions through multiple pathways, not only by lowering NO₃⁻ accumulation, but also by directly suppressing AOM abundance. Notably, the total effect of soil, which integrates site and NI treatments on AOMs, was stronger than its direct effect on N₂O, underscoring the importance of microbial mediation as a central mechanism of NI efficacy. Among all drivers, soil NH₄⁺-N and pH were the two dominant variables influencing total N₂O emissions, with NH₄⁺-N serving as the primary stimulator of AOM growth, and pH exerting a critical direct suppression on N₂O release.

5. Conclusions

This study demonstrated the strongly soil-dependent efficacy of three common nitrification inhibitors (NIs) in mitigating N₂O emissions in two typical tea plantation soils. Across both soils, all NIs effectively delayed NH₄⁺ depletion and suppressed NO₃⁻ accumulation, yet their performance varied substantially with specific soil properties such as pH, texture, and SOC content. Nitrapyrin consistently provided the strongest and most reliable N₂O suppression, whereas DCD and DMPP exhibited a more variable, soil-specific effectiveness.

Mechanistically, NIs reduced N₂O emissions not only by regulating substrate availability but also through the direct suppression of ammonia-oxidizing microorganisms (AOMs). Our results further indicated that AOA played a dominant role in nitrification in the strongly acidic soil, whereas multiple nitrifier groups contributed under moderately acidic conditions. These findings highlighted the importance of tailoring NI selection to local soil properties and microbial community composition. However, given that these conclusions are derived from a controlled laboratory incubation using only two specific soils, their broader applicability remains to be verified by field validation under realistic climatic conditions in the future.