Nitrogen, Phosphorus, and Potassium Adsorption and Desorption Improvement and Soil Buffering Capacity Using Clinoptilolite Zeolite

: The physical and chemical properties of clinoptilolite zeolite can be used to enhance soil nutrient availability for optimum crop use. Amending nitrogen, phosphorus, and potassium fertilizers with clinoptilolite zeolite could create a pool of negative charges to retain and release nutrients timely for crop use. Thus, we used clinoptilolite zeolite to enhance Typic Paleudults sorption (adsorption and desorption) of nitrogen, phosphorus, potassium, and this soil’s pH buffering capacity. The treatments evaluated were: (i) 250 g soil alone, (ii) 20 g clinoptilolite zeolite alone, (iii) 250 g soil + 20 g clinoptilolite zeolite, (iv) 250 g soil + 40 g clinoptilolite zeolite, and (v) 250 g soil + 60 g clinoptilolite zeolite. Clinoptilolite zeolite increased soil nitrogen and potassium adsorption, nitrogen desorption, and soil pH. Moreover, ability of the soil to resist drastic change in pH (pH buffering capacity) was improved. Additionally, phosphorus adsorption and desorption of phosphorus and potassium were reduced. Higher potassium adsorption with lower potassium desorption suggests that the clinoptilolite zeolite sorbs potassium effectively. The clinoptilolite zeolite nitrogen, phosphorus, and potassium contributed to the reduction in the adsorption these nutrients. The clinoptilolite zeolite improved nitrogen, phosphorus, and potassium availability and soil buffering capacity to prevent these nutrients from being ﬁxed or lost through for example, leaching. Therefore, clinoptilolite zeolite application could contribute to improved use of nitrogen, phosphorus, and potassium fertilizers to prevent soil, air, and water pollution. Additionally, our intervention could improve nitrogen, phosphorus, and potassium use efﬁciency.


Introduction
Nitrogen (N), phosphorus (P), and potassium (K) are important nutrients for crop productivity. These nutrients are made available in soils through sorption processes, such as absorption and adsorption. The mechanism through which positively charges ions adsorbed by the negatively charged parts of soils among others is referred to as adsorption [1,2] whereas the release of adsorbed ions is called desorption [3,4]. Apart from ensuring NH 4 + retention in soils, adsorption improves N use efficiency of crops in addition to preventing leaching of NH 4 + and nitrate (NO 3 − ) to contaminate water bodies which commonly causes algae bloom. The adsorption of K + using clinoptilolite zeolite (CZ) is similar to NH 4 + . Thus, the technology for extracting K + from seawater using CZ as an adsorbent has been adopted into industrial operation [5]. However, for anion such as phosphate (PO 4 3− ), surfactant-modified zeolites could be used to remove P anionic through adsorption. Reports from several studies suggest that surfactant-modified zeolite adsorbs anions such as NO 3 − , sulphate (SO 4 2 ), chromate (CrO 4 2− ), and hydrogen arsenate (HAsO 4 2− ) [6], CrO 4 2− [7,8], and HAsO 4 2− [9]. The nutrients that are adsorbed in soils are readily used by crops than the absorbed ones and Langmuir, Freundlich, and Temkin methods are commonly used to measure these fractions. The amount of nutrients in the form of a single layer on the soil surface is measured using Langmuir isotherm suggesting that this method is suitable for single layer surface adsorption reaction for adsorption sites that are fixed [10,11]. Freundlich isotherm demonstrates how adsorbed nutrients and adsorbent surface are related based on the premise that different sites or heterogeneous adsorbent surface with many adsorption energies exist [12]. The binding energy involved in adsorbing nutrient is measured by Temkin isotherm based on the assumption that heat generation during the process of nutrient adsorption decreases linearly as the adsorbent coverage increases, following the interaction among the adsorbates (uniform binding energy controls how nutrients are adsorbed) [13,14].
Soil buffering capacity is one of the determinant factors that affects adsorptions of nutrients [15]. Initial soil pH, amount of acid or alkali, and soil pH buffering capacity are the most important factors that control soil pH. Soil pH resilience is controlled by several chemical reactions such as protonation or deprotonation of acidic compounds and ion exchange [16]. Leaching loss of N and K because of poor soil retention has adverse effect on soil acidity. Ultisols and Oxisols are acid soils with pH 4 to 5, less fertile, low in cation exchange capacity (CEC), and high kaolinite and sesquioxides (oxides of Fe and Al). Phosphorus is not available in acid soils partly because of P fixation [17]. However, Ultisols and Oxisols can be productive when limed, fertilized, and conditioned or amended with CZ.
Amending low pH soils with CZ improves their pH and the productivity of crops [18] because of the neutralizing ability of CZ, the ion-exchange of CZ, and the affinity of CZ for water and positively charge ions [3]. In other related studies, Peres-Caballero et al. [19] described zeolites as crystalline hydrated aluminosilicates whose size ranges from 0.3 to 1 nm upon being in contact with water and this property has compelled researchers to believe that zeolites qualify as a sieving materials with unique nutrient (for example, NH 4 + and K + ) selection ability [19,20]. The selective nutrient adsorption nature of zeolites also ensures timely release of adsorbed nutrients (for example, NH 4 + and K + ) in a manner is that in synchrony crop needs to guarantee nutrient use efficiency in sustainable farming systems [21][22][23]. The cation exchange property of zeolites have been exploited to sorb NH 4 + and K + from aqueous solution in addition to using the pores of aluminosilicate groups in zeolites to adsorb cations. In terms of soil P and soil acidity management, capitalizing on the CEC and pH of CZ might not only reverse P fixation but it will also increase soils pH. Based on these rationales, our premonition is that amending acid soils with CZ will improve soil pH resilience, N, P, and K availability besides minimizing P fixation by Al and Fe.
Although CZ, if used as adsorbent for NH 4 + and K + , can complement to chemical fertilization and liming programs, the literature is not replete with data on how acid soils could be amended with CZ to significantly improve N, P, and K availability. To this end, this present study addressed the following research questions: (i) Is it possible to use CZ to amend acid soils' to significantly improve retention of N, P, and K in addition to improving soil pH resilience and, (ii) what is the optimum rate of CZ that improve acid soils' N, P, and K availability and buffering capacity? To answer the afore-stated research questions, the objectives of this study were to determine the effects of amending Bekenu Series (Typic Paleudults) with CZ on adsorption and desorption of N, P, and K, soil pH, and soil pH buffering capacity. Studies on nutrients adsorption such as N, P, and K and soil pH buffering capacity using CZ as soil amendment are essential in determining soil response to N, P, and K additions and the capacity to buffer the net inputs of acid. The implications of including CZ as a soil amendment is an attempt to delay nutrients migration out of farms. With our intervention, fertilizer applications following using CZ at optimum amount, leaching loss of nutrients such as N, P, and K could be prevented. This study also provides information on the mechanism of N, P, and K adsorb and desorb reflected by the different sorption isotherms and the capacity of Bekenu Series (Typic Paleudults) to buffer the changes in pH from acidity input.

Soil Sampling, Preparation, and Selected Physico-Chemical Analyses
A Typic Paleudults (Bekenu Series) soil located at Universiti Putra Malaysia Bintulu Sarawak Campus, Malaysia ( Figure 1) was sampled at 0 to 25 cm, after which the soil was prepared using standard procedures for the sorption studies. Details about the experimental site has been published in one of our papers [24].
Agronomy 2021, 11, x FOR PEER REVIEW 3 of 20 to N, P, and K additions and the capacity to buffer the net inputs of acid. The implications of including CZ as a soil amendment is an attempt to delay nutrients migration out of farms. With our intervention, fertilizer applications following using CZ at optimum amount, leaching loss of nutrients such as N, P, and K could be prevented. This study also provides information on the mechanism of N, P, and K adsorb and desorb reflected by the different sorption isotherms and the capacity of Bekenu Series (Typic Paleudults) to buffer the changes in pH from acidity input.

Soil Sampling, Preparation, and Selected Physico-Chemical Analyses
A Typic Paleudults (Bekenu Series) soil located at Universiti Putra Malaysia Bintulu Sarawak Campus, Malaysia ( Figure 1) was sampled at 0 to 25 cm, after which the soil was prepared using standard procedures for the sorption studies. Details about the experimental site has been published in one of our papers [24]. Selected soil physical properties (Table 1) were determined using the method described by Tan [25]. pH of the soil was determined in a ratio of 1:2 (soil: distilled water suspension) using a pH meter. Soil total C, N, and organic matter were determined using a Leco carbon, hydrogen, nitrogen, and sulphur (CHNS) Analyzer (LECO Truspec Micro Elemental Analyzer CHNS, New York, NY, USA). Soil available P was extracted using the double acid method [25] followed by the molybdenum blue method [26]. Soil exchangeable Ca, Mg, and K were extracted using the leaching method [25] after which the contents of these cations were determined using Atomic Absorption Spectrophotometry (Analyst 800, Perkin Elmer, Norwalk, CT, USA). Soil cation exchange capacity was determined using the leaching method [25] followed by steam distillation. The method of Keeney and Nelson [27] was used to extract exchangeable NH4 + and available NO3 − after which the concentrations of these ions were determined using steam distillation. The selected physical and chemical properties of the soil (Bekenu Series, Typic Paleudults) that was used in the adsorption and desorption studies are comparable to those reported by Paramananthan [28] except for CEC, sand, silt, and clay contents. The selected chemical properties of the soil are summarized in Table 1. Selected soil physical properties (Table 1) were determined using the method described by Tan [25]. pH of the soil was determined in a ratio of 1:2 (soil: distilled water suspension) using a pH meter. Soil total C, N, and organic matter were determined using a Leco carbon, hydrogen, nitrogen, and sulphur (CHNS) Analyzer (LECO Truspec Micro Elemental Analyzer CHNS, New York, NY, USA). Soil available P was extracted using the double acid method [25] followed by the molybdenum blue method [26]. Soil exchangeable Ca, Mg, and K were extracted using the leaching method [25] after which the contents of these cations were determined using Atomic Absorption Spectrophotometry (Analyst 800, Perkin Elmer, Norwalk, CT, USA). Soil cation exchange capacity was determined using the leaching method [25] followed by steam distillation. The method of Keeney and Nelson [27] was used to extract exchangeable NH 4 + and available NO 3 − after which the concentrations of these ions were determined using steam distillation. The selected physical and chemical properties of the soil (Bekenu Series, Typic Paleudults) that was used in the adsorption and desorption studies are comparable to those reported by Paramananthan [28] except for CEC, sand, silt, and clay contents. The selected chemical properties of the soil are summarized in Table 1.     Table 2 are based on soil dry weight.

Clinoptilolite Zeolite Characterization
The CZ was purchased from MB Plus Sdn Bhd, Johore, Malaysia after which it analyzed for total N [29], exchangeable NH 4 + and available NO 3 − [27], pH, CEC [30], and exchangeable K, Ca, and Mg [30]. The results of these analyses are presented Table 2.

Determination of Nitrogen, Phosphorus, and Potassium Adsorption and Desorption
In total, three replications were used for the N, P, and K adsorption and desorption in this study. A 2 g soil was weighed into a 250 mL centrifuge bottle. Thereafter, 0, 50, 100, 200, 300, and 400 mg N L −1 ) N solutions prepared. These concentrations were prepared by dissolving ammonium chloride (NH 4 Cl) in 0.2 M NaCl. Afterwards, a 20 mL of the isonormal N solution was added to the centrifuge bottles to obtain 0, 500, 1000, 2000, 3000, and 4000 µg of added N sample −1 . The isonormal solution was used to preserve constant ionic strength in the mixtures (adsorbent and solution). Additionally, the isonormal solution was used to provide competing ions for exchange sites [31]. To de-activate micro-organisms activity, two drops of toluene were added to the samples [32] after which they were equilibrated for 24 h at 180 rpm on an orbital shaker, centrifuged at 10,000 rpm for 15 min, and N determined [30]. Nitrogen adsorbed per gram soil (µg g −1 soil) was calculated as the difference between the initial amount of N added and the amount in the equilibrium solution. After N adsorption, the samples were washed using ethanol followed by centrifugation at 10,000 rpm for 15 min [30] to discard the ethanol. Thereafter, a 20 mL of 2 M KCl was added, equilibrated for 24 h at 180 rpm on an orbital shaker followed by centrifugation at 10,000 rpm for 15 min. Afterwards, the desorbed N in the supernatant was determined [30].
The N adsorption procedure was used for the P adsorption but with some modifications. Phosphorus concentrations of 0, 50, 100, 200, 300, and 400 mg P L −1 were prepared by dissolving potassium dihydrogen phosphate (KH 2 PO 4 ) in a 0.01 M CaCl 2 solution, after which a 25 mL of the isonormal P solutions were added to the centrifuge bottles to obtain 0, 652, 1250, 2500, 3750, and 5000 µg of added P sample −1 . Following centrifugation at 10,000 rpm for 15 min, P in the supernatant was determined [26]. For the amount of P desorbed, the centrifuged samples were used where a 20 mL of 0.01 M CaCl 2 was added to the samples and equilibrated for 24 h at 180 rpm on an orbital shaker, centrifuged at 10,000 rpm for 15 min, and the P in the supernatants was determined [26] as desorbed P.
The N adsorption procedure was used for the K adsorption but with some modifications. Potassium concentrations of 0, 50, 100, 200, 300, and 400 mg K L −1 were prepared by dissolving potassium chloride (KCl) in 0.01 M CaCl 2 solution after which, a 20 mL of the isonormal K solution was added to the centrifuge bottles to give 0, 500, 1000, 2000, 3000, and 4000 µg of added K sample −1 , centrifuged at 10,000 rpm for 15 min after which the K in the supernatants were determined using atomic absorption spectrophotometery (AAS). For the amount of K desorbed, the centrifuged samples were used where a 20 mL of 0.01 M CaCl 2 was added to the samples and equilibrated for 24 h at 180 rpm on an orbital shaker, centrifuged at 10,000 rpm for 15 min, and the K in the supernatants determined using AAS as desorbed K.

Nitrogen, Phosphorus, and Potassium Adsorption Isotherms
Adsorbed N, P, and K of the samples tested in this study were fitted to Langmuir type 1, 2, 3, and 4, Freundlich, and Temkin adsorption isotherms as shown in Table 3 [32,33]. Table 3. Nonlinear and linear adsorption isotherms models used in this present study.

Isotherm Nonlinear Form Linear Form Plot Variables
Langmuir−1

Soil pH Buffering Capacity Determination
The different amounts of CZ and 250 g soil were thoroughly mixed as presented as follows: Soil: 250 g soil only CZ: 20 g CZ only CZ1: 250 g soil + 20 g CZ CZ2: 250 g soil + 40 g CZ CZ3: 250 g soil + 60 g CZ There were three replications in this soil pH buffering capacity study. The titration method was used to determine the soil and CZ pH buffering capacity [34] followed by plotting titration curves by increasing mmol H + kg −1 samples suspended in water. A 1:2.5 sample:water (w:v) ratio was used for soil alone, CZ, CZ1, CZ2, and CZ3. During the titration, 10 g of soil, CZ, CZ1, CZ2, and CZ3 were weighed into 100 mL plastic vials followed by adding 25 mL distilled water. Then, 1 mL 0.05 M CaCl 2 was added to the samples to minimize variations in ionic strength followed by adding 0.2 mL toluene to impede microbial activity [35]. Afterwards, the samples were equilibrated for 15 min at 180 rpm on an orbital shaker for seven days at 25 • C [35][36][37] after which a digital pH meter (SevenEasy pH, Mettler-Toledo GmbH, Switzerland) was used to determine the pH of the samples. For the samples, whose initial pH were less than 5.5, a 0.1 M NaOH was added using Eppendorf pipette to reduce suspension effect [34]. A 0.1 M HCl was used for the samples whose initial pH were greater six or were slightly acidic to basic. For all of the samples, 1, 2, 3, 4, 6, 8, and 10 mL of 0.1 M HCl or 0.1 M NaOH were used. The suspensions were stirred using a glass rod for 10 s following addition of 0.1 M HCl or 0.1 M NaOH. Thereafter, the pH of the suspensions were determined using a digital pH meter. The amount of mmol H + needed to change pH by one unit was calculated as the negative reciprocal of the slope of the linear regression based on sample pH (Y-axis) and addition rate of mmol H + kg −1 sample (X-axis): Sample pH buffering capacity (mmol H + kg −1 sample) = − 1 slope (1) where, slope = fitted slope of linear regression line for each sample.

Experimental Design and Statistical Analysis
The treatments were arranged in a completely randomized design (CRD) with three replications and their effects were detected using analysis of variance followed by treatment means separation using Tukey's Test at p ≤ 0.05. A simple linear regression was used to obtain the coefficient of determination (R 2 ). These statistical tests were carried out using the Statistical Analysis System version 9.2 [38]. The N, P, and K adsorption isotherm equations were subjected to Chi-square analysis to obtain best-fit isotherm. The isotherm model with the smallest chi-square value was deemed the best best-fit isotherm. The stated formula was used for the Chi-square value calculation: where, q e is the equilibrium capacity from the experimental data and q e,m is the equilibrium capacity obtained by calculation from model.

Nutrient Concentrations in Equilibrated Samples
The treatments and added N, P, and K interacted (Tables 4-6). Irrespective of treatment, the concentrations of N, P, and K in the equilibrated samples increased as the amounts of N, P, and K increased (Tables 4-6). For CZ only, lower N and K was observed. Increasing rate of the CZ decreased N and K remaining in the equilibrated solution, however, it increased the remaining P in the equilibrated solution (Tables 4-6). Regardless of the amount of P used, P in the equilibrated samples were similar (Table 5). Nitrogen and K in the equilibrated samples decreased with the increasing amount of the CZ (Tables 4 and 6).   Irrespective of treatment (soil alone, CZ alone, CZ1, CZ2, and CZ3), there was a linear relationship between the added amounts of N, P, and K and the contents in the equilibrated samples ( Table 7), suggesting that N, P, and K contents in the equilibrated samples increased with the increasing amounts of N, P, and K used. Table 7. Linear relationships between the added amounts nitrogen, phosphorus, and potassium and their contents in the equilibrated samples.

Treatment
Regression

Adsorption Isotherm of Nitrogen, Phosphorus, and Potassium
Adsorption of N and K were higher in all treatments with CZ compared with soil alone (Tables 8-10).   Irrespective of the samples tested, there was an increase in adsorptions in the amounts of N, P, and K adsorbed ( Table 11). The CZ showed higher N and K adsorption rates but lower P adsorption rate compared with soil alone (Table 11). Table 11. Linear relationships between the added nitrogen, phosphorus, and potassium concentrations and the amounts of nitrogen, phosphorus, and potassium adsorbed.

Nitrogen, Phosphorus, and Potassium Adsorption Isotherms
The intercepts for types 1, 2, and 3 of Langmuir N adsorption isotherms were negative ( Table 12). Regardless of treatment, the N adsorption experimental data best fitted with Freundlich and this observation is related the significant R 2 and lower χ 2 value (Table 13). This is unlike those with Langmuir (type 4) and Temkin adsorption equations (Table 13).
High antilog (intercept) K F values (N adsorption) were observed in CZ alone, CZ1, CZ2, and CZ3 compared with soil alone (Table 14). Table 12. Fitting Langmuir type 1, 2, and 3 isotherms to the nitrogen adsorption data based on simple regression and Chi-square analyses results.

Treatment
Regression Equation   The P adsorption data for soil alone, CZ alone, CZ1, CZ2, and CZ3 best fitted with Langmuir type 2 isotherm, based on significant R 2 and lower χ 2 values (Table 15) and this is in contrast to those of Freundlich and Temkin (Table 16). The treatment without CZ (Soil only) demonstrated the highest bonding energy constant (K L ) for P adsorption (Table 17). Table 15. Fitting Langmuir type 1, 2, and 3 isotherms to the phosphorus adsorption data based on simple regression and Chi-square analyses results.

Treatment
Regression Equation         The soils with the CZ (CZ1, CZ2, and CZ3) best fitted with Langmuir type 2 isotherm because of the lower χ 2 value (Tables 18 and 19). Potassium adsorption data for soil only and CZ alone best fitted best with Freundlich due to the significant R 2 and lower χ 2 values (Table 19). Langmuir bonding energy constant (KL), maximum adsorption capacity (qm), and maximum buffering capacity (MBC) of K adsorption were determined from Langmuir type 2 equations for CZ1, CZ2, and CZ3 (Table 20). Table 18. Fitting Langmuir type 1, 2, and 3 isotherms to the potassium adsorption data based on simple regression and Chi-square analyses results.

Treatment
Regression  Note: Two ** indicate significant relationship at p = 0.01. One * indicates significant relationship at p = 0.05. ns indicates not significant at p = 0.05. Table 19. Fitting Langmuir type 4, Freundlich, and Temkin isotherms to the potassium adsorption data based on simple regression and Chi-square analyses results.   Regardless of treatment, N and P desorption in relation to N and P concentrations were linearly related (Table 21). The fact the desorption amounts of N and P were higher for CZ only compared with soil only suggest that the CZ can release N and P into solution (Table 21). Table 21. Linear relationships between the added amounts nitrogen, phosphorus, and potassium and their amounts desorbed.   Figure 2 summarizes the effects of soil only, CZ only, and soil with different amounts of CZ (CZ1, CZ2, and CZ3) on the pH buffering capacity of the soil. Regardless of treatment, the soil pH and added mmol H + related negatively (Figure 2). The pH and pH buffering capacity of the soil without clinoptilolite zeolite were lower because of the lower organic matter content and CEC of the soil (Table 22).

Nitrogen, Phosphorus, and Potassium in Equilibrium Solution
Increasing or no significant N or P or K contents in the equilibrium solution with increasing CZ rate demonstrate that the addition of CZ did not increase nutrient adsorption (Tables 4-6). The decreasing N or P or K contents in the equilibrium solution with increasing CZ rate indicates that the addition of the CZ increased these nutrients' adsorption (Tables 4-6). Compared with soil only, CZ only showed lower N, P, and K contents in the equilibrium solution of the no N, P, and K addition suggest that CZ had low exchangeable NH4 + , K, (Tables 4 and 6), and available P ( Table 5). The decreasing rate of N or P or K remaining in the equilibrium solution with increasing amount of the CZ suggests that the use of increased the adsorption of these nutrients. However, the increasing or

Nitrogen, Phosphorus, and Potassium in Equilibrium Solution
Increasing or no significant N or P or K contents in the equilibrium solution with increasing CZ rate demonstrate that the addition of CZ did not increase nutrient adsorption (Tables 4-6). The decreasing N or P or K contents in the equilibrium solution with increasing CZ rate indicates that the addition of the CZ increased these nutrients' adsorption (Tables 4-6). Compared with soil only, CZ only showed lower N, P, and K contents in the equilibrium solution of the no N, P, and K addition suggest that CZ had low exchangeable NH 4 + , K, (Tables 4 and 6), and available P ( Table 5). The decreasing rate of N or P or K remaining in the equilibrium solution with increasing amount of the CZ suggests that the use of increased the adsorption of these nutrients. However, the increasing or similar rate of P or K remaining in the equilibrium solution with increasing amount of the CZ suggests that the addition of the CZ in Typic Paleudults did not maximize adsorption of these nutrients (Table 7). In contrast to the use of natural zeolite as an ammonia adsorbent and N carrier, adsorption capacity of natural zeolite increases with the initial NH 4 + solution concentration [39]. Different type of zeolites affect adsorption capacity differently. For example, zeolite prepared from raw fly which has a slow adsorption capacity for NH 4 + , and its application is in fields with high concentration wastewater is limited [40]. In this present study, the different amounts of CZ used for N, P, and K adsorption affected the N, P, and K in equilibrium solutions and this observation is consistent with the findings of Tang et al. [40] who also reported that adsorption equilibrium between adsorbent and adsorbate is controlled by the adsorbent dosage.

Nitrogen, Phosphorus, and Potassium Adsorption Isotherms
The increased adsorbed N with the increasing rate of the CZ suggests that the CZ can improve N adsorption (Table 8). However, the similar adsorbed P or K with the increasing rates of the CZ indicates that the lowest rate of CZ was sufficient for the adsorption of P and K ( Table 9). The higher cations (NH 4 + and K + ) and lower anion (phosphate) adsorption rates of the treatments with CZ was because of the negative charges of the CZ but the opposite was true for P which might have been repelled [41]. The increasing rates of CZ (CZ1 < CZ2 < CZ3) increased cations (NH 4 + and K + ) adsorption (Tables 8 and 10) because of the higher CEC of the CZ. However, the CZ (CZ1 < CZ2 < CZ3) treatments reduced P adsorption because of the negative-negative charge coulumbic repulsive forces [42].
The higher adsorbed N or P or K in the CZ only treatment compared with soil only was due to the high CEC of the CZ whereas, the lower adsorbed P in CZ compared with soil only was due to anionic nature of CZ (Tables 8-10). The coulumbic repulsive forces (same charge repulsion) of the CZ might have reduced the ability of the soil to adsorbed P [43]. Adsorbed N increased with increasing rates of CZ (CZ1 < CZ2 < CZ3) (Table 8). However, the increasing rates of CZ (CZ1 < CZ2 < CZ3) showed similar adsorbed P (Table 9). Adsorbed K was not affected by the increasing rates of CZ (CZ1 < CZ2 < CZ3) ( Table 10). The higher rates of adsorption for N and K but not P were because of CZ has affinity for NH 4 + and K + ( Table 11). The fact that the experimental data of Langmuir N adsorption isotherms type 1, 2, and 3 exhibited negative intercepts (Table 12) suggest that the tested Langmuir isotherms type 1, 2, and 3 for N adsorption regardless of treatment contradict or are inconsistent with the underlying Langmuir assumption [37]. Freundlich isotherm suggests that the adsorbed N of the treatments occurred at heterogeneous adsorbent surface of samples (Table 13) [11]. High K F values of CZ alone, CZ1, CZ2, and CZ3 compared with soil alone suggests that the CZ has higher N adsorption capacity because of its higher CEC (Tables 13  and 14). In addition, the 1/n > 1, regardless of treatment suggests that the N adsorption is not a favorable adsorption reaction [33]. Langmuir P adsorption isotherm for soil only, CZ only, CZ1, CZ2, and CZ3 (Tables 15-17) suggests that P was adsorbed by formation of a monolayer on the outermost surface of the adsorbent [10,11]. Irrespective of treatment, the highest bonding energy constant (K L ) for P adsorption of soil only (Table 17) was due to precipitation of P by exchangeable Al 3+ [41] because highly weathered tropical soils have anion exchange capacity to adsorb anions such as phosphates [42]. In addition, CZ alone, CZ1, CZ2, and CZ3 showed lower K L compared with soil alone (Table 17) because of the high CEC of the CZ and this means the negative charges of the afore-stated amendment might have repelled phosphates [41].
According to the literature, the maximum mass adsorbed at saturation conditions per mass unit of adsorbent in monolayer manners where, high q m requires less P saturation maximum mass adsorbed at saturation conditions per mass unit of adsorbent is referred to as maximum adsorption capacity (q m ) [44]. Therefore, the higher maximum adsorption capacity (q m ) of CZ only relative to soil only (Table 17) suggests that CZ only needs less P for adsorbent saturation because the negatively charged exchange sites of the CZ only repelled P. Similarly, q m of CZ1, CZ2, and CZ3 compared with soil alone shows that the CZ treatments (CZ1, CZ2, and CZ3) required similar P to saturate the adsorbent. The lower q m of soil, CZ1, CZ2, and CZ3 compared with CZ alone was because of the lower P content in the soil. Maximum buffering capacity (MBC) of P is the level at which adsorbent replenishes P to sample solution because being inclined depletion [45] and this lend to support or add credence the reason why soil only significantly release P relative to CZ alone, CZ1, CZ2, and CZ3 (Table 17).
The treatment with the lower rate of CZ (CZ1) showed lower K L compared with those with higher rate (CZ2 and CZ3) because of the lower K content of the CZ but higher CEC (Tables [18][19][20]. The affinity of the CZ was higher at the higher rate of CZ. Increasing rate of CZ (CZ1 < CZ2 < CZ3) increased q m because lower amount of K was required to saturate the adsorbent. This was possible because of the inherent or native K of the CZ compared with soil alone. The increasing rate of CZ (CZ1 < CZ2 < CZ3) increased MBC because of the higher CEC of the CZ. The higher K F value of CZ only compared with soil only was due to the high CEC of the CZ (Table 20). The 1/n < 1 for soil only and 1/n ≈ 1 for CZ only suggest favorable K adsorption ( Table 20). The high N or P or K desorption rates of the CZ suggest they can temporary retain these nutrients although the CEC of the CZ is high. The lower K desorption rate (Table 21) but higher K adsorption capacity of CZ only (Table 20) compared with soil only suggests that sorption of K by CZ was more to absorption.

Nitrogen, Phosphorus, and Potassium Desorption
The increasing rate of the CZ (CZ1 < CZ2 < CZ3) increased N desorption rate (Table  21) because of the lower affinity of the CZ for NH 4 + compared with K + [46]. The increasing rate of the CZ (CZ1 < CZ2 < CZ3) reduced P and K desorption rate. The reduction in P desorption rate with the increasing CZ rate is consistent with the reduced maximum buffering capacity (Table 17) where, adsorbed P were not readily replenished during P depletion in the soil following the application of CZ. Hence, CZ can be used to reduce P leaching. The increasing maximum buffering capacity (Table 20) with decreasing K desorption rate upon increasing CZ application suggests that K was more to absorption compared with adsorption, hence, the lower desorption. Absorption of K is further supported by the fact that the CZ demonstrated higher affinity for K + compared with other cations [47].

Clinoptilolite Zeolite and Bekenu Series Soil Buffering Capacity
The soil pH buffering capacity is typical of those of highly weathered soils (9 to 27 mmol kg −1 pH −1 ) [34]. pH buffering capacity of the CZ only was higher than that of soil only due to the high CEC of the CZ. The increasing rate of the CZ (CZ1 < CZ2 < CZ3) increased soil pH and pH buffering capacity because of the high pH and pH buffering capacity of the CZ (Figure 2 and Table 22). The pH buffering capacity soil only and the soil with different amounts of CZ were within the standard range of 10 to 100 mmol H + kg −1 pH −1 [33].

Conclusions
Clinoptilolite zeolite can increase N and K adsorption, N desorption rate, soil pH, and pH buffering capacity irrespective of amount of CZ added. Additionally, it can reduce P adsorption and desorption of P and K. Higher K adsorption with lower K desorption suggests that the CZ sorbs K effectively. The fact soil N and K adsorption and P desorption were improved, regardless of the amount of CZ added to the soil, indicates that the lowest rate of CZ was sufficient for the retention of total N and K and desorption of P. Therefore, for the optimum rate, soil amended with 20 g of CZ is recommended to improve retention of soil total N and K and P desorption instead of CZ at 40 and 60 g. Apart from the liming effect, CZ hindered re-acidification of amended Bekenu series soil by increasing soil pH buffering capacity. The limitation of the N, P, and K adsorption and desorption study is that it was not based on the conventional fertilization for N, P, and K. However, the data have been tested in different isotherms such as Langmuir, Freundlich, and Temkin and these three isotherms confirmed the validity of CZ that could be used in N, P, and K retention and availability of N, P, and K.