ISSN e: 2007-4026 / ISSN print:2007-3925

### Volume 11, Issue 2 July - December 2019

ISSN: ppub: 2007-3925 epub: 2007-4026

Scientific article

# Nutrient balance in maize cropping systems and challenges for their sustainability

http://dx.doi.org/10.5154/r.inagbi.2017.11.017

Flores-Sánchez, Diego 1 * ; Navarro-Garza, Hermilio 1 ; Pérez-Olvera, Ma. Antonia 1

Corresponding author: dfs@colpos.mx, tel. 01 595 9520200, ext. 1853.

Received: November 26, 2017; Accepted: March 07, 2019

## Introduction:

Nutrition management in the maize crop in Guanajuato, Mexico, is based on mineral fertilization, with high doses of nitrogen and reduced application of phosphorus and potassium.

## Objective:

To diagnose the management of mineral nutrition and residues from the maize cropping system, and identify opportunities for their efficient use.

## Methodology:

68 maize farmers from the municipalities of Salvatierra and Valle de Santiago, Guanajuato, were surveyed. Plot soils were sampled, and yield, nutrient concentration and C mineralization were estimated. With the data obtained, graphs of the balance of N, P, K and C were made.

## Results:

Nutrition management and biomass production varied among farmers. Currently, P and K are not limiting factors, unlike N, since the soil only contributes 11 % of the total available nitrogen. Residue management showed that there is an imbalance between soil C mineralization and the incorporation of residues.

## Study limitations:

The analysis focused on only one agricultural cycle.

## Originality:

The focus of the study, including the graphical analysis, is scarcely applied in the region’s maize farming systems.

## Conclusions:

An integral vision is required for the management of organo-mineral nutrition and residues to contribute to their efficient and sustainable use.

Keywordsnitrogen; phosphorus; potassium; carbon; residues; nutrient use efficiency; Guanajuato

## Introduction

Today, agriculture faces a number of challenges associated with the environmental and social crisis, the growing technology gap, the privatization of public research and higher education entities, and socio-economic inequity, among others (International Assessment of Agricultural Knowledge, Science and Technology for Development [IAASTD], 2009). In Guanajuato, as well as in several regions of Mexico, so-called "conventional agriculture" is promoted and developed, which privileges the productivity of labor and invested capital as principles to increase the yield of the land, although with great effects on ecological fragilization and desertification, with an unfavorable impact on the heritage of material resources (Gomiero, Pimentel, & Paoletti, 2011).

In Guanajuato, Mexico, cereal cropping systems (such as for maize, sorghum, wheat and barley) cover an area of 671 764 ha, representing more than 70 % of the state's agricultural area. In 2017, records show maize was cultivated in an area of 453 599 ha, accounting for 67 % of all land cultivated with cereals (Servicio de Información Agroalimentaria y Pesquera [SIAP], 2015). Cereal cropping systems, particularly of maize, are managed under an intensive conventional model. This model is characterized by a rotational pattern (predominantly cereal-cereal), in addition to the burning and removal of crop residues, resulting in the sending of carbon emissions into the atmosphere and decapitalization of organic matter and carbon from local farming systems in very significant amounts (Grageda-Cabrera et al., 2004). This has resulted in a severe deterioration of soil fertility (Báez-Pérez, Arreola-Tostado, Triomphe, Bautista-Cruz, & Licea-Morales, 2014) and a continuous increase in production costs due to the need to correct the problems caused.

Maize crop nutrition is one of the main components of the production process, and has been managed through the application of chemical fertilizers, which is characterized by high doses of nitrogen, reduced application of phosphorus and negligible use of potassium; however, this can lead to nutritional imbalances and inefficiencies in their use (Jat et al., 2013; Vitousek et al., 2009). Additionally, the intensification of conventional tillage systems and their intervention with wet horizons have caused soil compaction, resulting in reduced root growth, low fertilizer recovery efficiency and crop productivity risks.

The above scenario demands an improvement in the logic of nutrient use that promotes more sustainable farming systems. The evaluation of the nutrient balance is a tool that allows having the necessary elements to promote efficient nutrient use, maximize crop productivity and conserve resources (Cassman, 2003; Doré et al., 2011). This management strategy is a current need among farmers considering that fertilizers represent about 50 % of production costs (Pérez-Espejo, Jara-Durán, & Santos-Baca, 2011), since it would contribute to a considerable reduction in the resources invested in maize production. Therefore, the objective of the research was to diagnose the management of mineral nutrition and residues from the maize cropping system, and identify opportunities for their efficient use.

## Materials and methods

The research was conducted in communities in the municipalities of Valle de Santiago (20° 23’ NL and 101° 11’ WL) and Salvatierra (20° 00’ NL and 100° 47’ WL), during 2012 and 2014, respectively, both belonging to Guanajuato, Mexico. The methodological approach comprised the following stages:

## Characterization of regional production systems

In Valle de Santiago we worked with 55 maize cropping systems and in Salvatierra with 13 systems of the same type. Surveys were conducted in both municipalities to characterize the types of technical maize itineraries.

## Sampling of cropping systems

a) Soil. In the selected cropping systems, 10 soil subsamples per hectare were taken, at a depth of 0 to 20 cm, after which a composite sample was taken for laboratory analysis. The properties analyzed were pH (1:2, soil:water), organic matter (Walkley-Black method), total nitrogen (Kjeldahl-N method), phosphorus (Olsen), interchangeable potassium (in ammonium acetate, pH 7.0) and cation exchange capacity (ammonium acetate, pH 7).0) with the methods specified in Mexican standard NOM-021- SEMARNAT-2000 (Secretaría del Medio Ambiente y Recursos Naturales [SEMARNAT], 2000), and carbon content was estimated from the organic matter value obtained. Table 1 presents the average results for each municipality.

Table 1. Average soil property values of maize cropping systems in Valle de Santiago and Salvatierra, Guanajuato, Mexico.

Municipality Statistic pH OM1 C Nt P
(mg·kg-1)
K
(cmol·kg-1)
CEC
(meq·100 g-1)
(g·kg-1)
Valle de Santiago (n = 55) Average 7.7 34.2 19.8 1.70 21.7 1.8 49.9
SD 0.38 6.2 3.6 0.31 15.9 0.66 7.31
Range 6.7-8.3 19.0-48.0 11.0-27.8 0.9-2.4 5.2-82.5 0.7-4.4 32.5-66.5
Salvatierra (n = 13) Average 7.6 18.3 10.6 0.97 15.9 1.94 38.7
SD 0.32 4.3 2.5 0.24 11.3 0.81 10.7
Range 7.3-8.2 10.8-26.0 6.3-15.1 0.6-1.4 7.7-56.3 0.71-3.6 19.0-50.0
1OM = organic matter; C = carbon; Nt = total nitrogen; P = phosphorus; K = potassium; CEC = cation exchange capacity; SD = standard deviation.

b) Biomass. To estimate the total aerial biomass, three sampling areas (3 linear meters each) were randomly selected in each cropping system in which the population density was measured. All plants in the sampling unit were cut at ground level and weighed in the field, then the cobs were separated and their total fresh weight was obtained. Three plants were randomly selected from the cut plants, weighed and dried in an oven at 70 °C for 48 h to determine moisture content and dry weight, after which total biomass and grain yield were estimated. Plant organs (leaves and stems) and grains were separated from these three plants and sent to the laboratory for analysis of their N, P and K content. Total nitrogen was analyzed with the semi-micro Kjeldahl technique (Bremner, 1965), while P and K were determined by inductively coupled plasma spectrometry (Varian Liberty Series II ICP-AES, Varian®, USA) (Alcántar & Sandoval, 1999).

## Information analysis

a) Nutrient extractions. The N, P and K content in the vegetative biomass and grains of the three plants analyzed was multiplied by their respective biomass produced (kg DM·ha-1), and then added to obtain the total extraction of nutrients.

b) Contribution of nutrients (N, P and K) from the soil and fertilizers. The availability (f) of N, P and K, and the potential soil contribution of these nutrients (SN, SP and SK, respectively) were calculated according to the Quantitative Evaluation of the Fertility of Tropical Soils (QUEFTS) model (Janssen et al., 1990; Sattari, van Ittersum, Bouwman, Smit, & Janssen, 2014):

f N = 0.25 ( p H - 3 )

f P = ( 1 - 0.5 ) ( p H - 6 ) 2

f K = 0.625 ( 3.4 - 0.4   p H )

S N = N 68   f N

S P = 0.35 f P ( C + 0.5   P )

S K = K ( 400   f K ) 2   ( 0.9   C )

where C is the soil organic carbon (g·kg-1), assuming that this represents 58 % of the organic matter content of the soil, N is the total nitrogen (g·kg-1), P is the available phosphorus (mg·kg-1), K is the interchangeable potassium (cmol·kg-1) and the pH is that of the soil. The efficiency of fertilizer recovery used was: N = 0.4, P = 0.2 and K = 0.4 (Bruulsema, Fixen, & Snyder, 2004; Ghosh, Singh, & Mishra, 2015; Peña-Cabriales, Grageda-Cabrera, & Vera-Núñez, 2001).

c) Mineralization of soil organic carbon (SOC) and residues. The mineralization coefficient of Henin and Dupuis (1945) (K2) was used for clay soils; in the residues, it was assumed that 45 % of these were carbon. The isohumic coefficient (K1) of 0.12 (Soltner, 1990) was used to estimate organic matter humification. Based on the available residues, three retention scenarios were made: 100, 50 and 30 %.

## Contributions for the analysis of N, P and K management in the soil

In the maize cropping systems of Valle de Santiago and Salvatierra, great variation in grain yield was found (between 7 300 and 15 800 kg·ha-1), with no association between nutrient availability and grain yield (Figure 1). This questions the existence of a variety of limiting factors (abiotic, biotic and their interactions) that eventually act on biological growth for biomass production and yield.

The amount of available nitrogen varied widely (from 86 to 284 kg N·ha-1) (Figure 1A), although most farming systems were concentrated in the range of 134 to 236 kg N·ha-1. The application of this nutrient via fertilization ranged from 71 to 554 kg N·ha-1, a situation that was more evident in Valle de Santiago. In the case of phosphorus (Figure 1B), its availability varied between 8 and 91 kg P·ha-1; however, the highest availability was between 28 and 75 kg P·ha-1, and only 10 % of the cropping systems were greater than 70 kg P·ha-1. It is important to point out that the dose of phosphorus applied through fertilizers was on average 45 kg P·ha-1, with a range of variation between 26 and 92 kg P·ha-1.

Most cropping systems had high availability of potassium (Figure 1C), since this nutrient is abundant in the region (Table 1), which implies little need for its application. However, in 57 % of the cases evaluated, potassium fertilizers are applied, with doses varying from 18 to 50 kg K·ha-1. It is important to note that the needs for this nutrient for maize cultivation are usually similar to those of nitrogen (Cruzate & Casas, 2003), so these inputs contribute in a certain way to reducing the short- and medium-term decapitalization of potassium in the soil.

On the other hand, the balance of N, P and K (extraction vs. availability) showed different trends among them (Figure 2). In the case of nitrogen (Figure 2A), it can be seen that in 59 % of the cropping systems the extraction was lower than the availability, in 29 % of the cases the extraction was higher than the availability and in 12 % there was a balance condition. In addition, 90 % of the cropping systems had between 150 and 250 kg·ha-1 of available nitrogen, and about 80 % of these extracted between 100 and 200 kg·ha-1. The average dose of nitrogen applied was 309 kg·ha-1, and the amount of unused nitrogen ranged from 7 to 195 kg·ha-1. In general, 89 % of the nitrogen supply to the system corresponds to fertilizers, which indicates the low availability of this nutrient in the soil. It is estimated that the region consumes around 330 thousand tons of nitrogen per year, with a recovery efficiency of 20 to 40 % (Peña-Cabriales et al., 2001). Considering the results and assuming a recovery efficiency of 40 %, losses may be associated with the form and timing of application, volatilization, immobilization and leaching (Grageda-Cabrera et al., 2011; Liu, Herbert, Hashemi, Zhang, & Ding, 2006).

It is important to note that there were not enough technical elements or agro-economic information to define the dose strategies and the timing of fertilizer application according to the phenological and reproductive states of maize. In general, two fertilizations are made, one in the sowing and the other 30 to 40 days afterwards; however, this can generate losses because they do not conform to the highest nutrient demand stages of maize. In the cases where the extracted N was higher than the available N, it is believed that the recovery efficiency could be higher than 40 %, in addition to which there are contributions via rain and mineralization of nitrogen from the soil and residues. Various studies in the region have shown that crops do not recover about 260 thousand tons of nitrogen, where 20 to 30 % is denitrified as nitrous oxide and molecular nitrogen, between 20 and 30 % is leached as nitrates, and 10 to 18 % is volatilized as ammonia (Grageda-Cabrera et al., 2011) and contributes 60 % of nitrogen dioxide (Montzka, Dlugokencky, & Butler, 2011; Reddy, 2015).

Due to the nature of nitrogen fertilizers, technical strategies aimed at reducing losses and improving recovery efficiency must be implemented. In this sense, adequate fertilization doses must be defined according to the yield objective and the available nitrogen in the soil; in addition, according to the maize demand curve, the application of fertilizers must be multi-fractionated, preferably three applications via mechanical means or fertigation (Andraski, Bundy, & Brye, 2000; Cueto-Wong et al., 2013; Paredes, Alamilla, & Mandujano, 2014).

In the case of phosphorus (Figure 2B), it was found that 87 % of the cropping systems had an extraction lower than the availability. Phosphorous recovery efficiency is of particular interest because it is one of the least available and mobile nutrients. Overall, annual recovery efficiency varies between 15 and 25 %; however, phosphorus tends to accumulate in the soil, mainly in cropping systems where annual applications of phosphorus fertilizers are made, a general situation in this case. In view of the above, recovery efficiency should be evaluated over the long term (Ghosh et al., 2015; Smil, 2000).

In the evaluated systems, 20 % of the extracted phosphorus comes from fertilizers and the rest is obtained from the soil, which indicates that there are sufficient reserves of this nutrient, since the average values in both municipalities are higher than 11 mg·kg-1 (Table 1). According to Mexican standard NOM-021-RECNAT-2000 (SEMARNAT, 2000), which establishes the specifications for soil fertility, salinity and classification, this value is high. Thus, phosphorus is not considered a limiting factor in Valle de Santiago and Salvatierra; however, phosphorus management should focus on nutrition records in order to maintain reserves and provide more efficient and cost-effective management of phosphorus fertilizers.

On the other hand, the potassium balance (Figure 2C) also indicated that the extraction (100 kg K·ha-1) was less than the availability, since on average 226 kg K·ha-1 were not used. The application of potassium is an uncommon and relatively new practice, considering that it was not included at the end of the 20th century. In this sense, it was recorded that 62 % of the farmers use it; however, they pointed out that potassium was not considered in their maize nutrition plan because they were unaware of the role it has in the crop. In addition, the soils of this region are characterized by having a high exchangeable potassium content (Table 1), a condition associated with their nature (Ramírez-Barrientos, Figueroa-Sandoval, Ordaz-Chaparro, & Volke-Haller, 2006), and it is sufficient to cover maize requirements. Several studies have observed a response in yield when applying this nutrient in potassium-rich soils (Aguado-Lara, Etchevers-Barra, Hidalgo-Moreno, Galvis-Spíndola, & Aguirre-Gómez, 2002), which could be associated with nitrogen availability.

Considering the results obtained, it is necessary to establish mechanisms to determine the antagonistic and synergistic effects between potassium and nitrogen (Zhang et al., 2010). In addition, in Mexico, and particularly for this type of soil, there is little information on potassium in soil-plant interaction, which suggests the need to investigate this and other elements in depth to improve the diagnosis of their presence in the soil (Aguado-Lara et al., 2002) and generate regional empirical models that allow having technical bases for their adequate and efficient use. Additionally, it is important to note that most of the potassium extracted by crops is concentrated in their vegetative parts, which indicates that residues are an important source of potassium. For this reason, a key element that contributes to increasing potassium levels in the soil is to incorporate the residues, since they can significantly promote the recycling of this nutrient in the cropping system (Zhang et al., 2010), with their consequent ecological and economic advantages in the durability of the regional system.

The behaviors recorded in Figures 1 and 2 show that there is differentiated management in the application of nutrients in the maize cropping system, which was also reflected in a generalized imbalance between the availability and extraction of N, P and K; this has implications for the reduction or depletion of essential nutrients (Cassman et al., 1996). However, in the soil there are reserves of P and K that cover maize’s demand, which indicates that currently they are not limiting factors for the production of this grain. On the other hand, N is a limiting factor because the soil only contributes 11 % of the total available nitrogen, and the rest is supplied through nitrogen fertilizers. The fractionation of nitrogen fertilization and its application according to its demand in the different phenological stages of maize are determining factors for an efficient use of fertilizers (Ali et al., 2005).

## Contributions for the analysis of soil C management

Grain production ranged between 7 300 and 16 100 kg·ha-1, and implicitly there is a similar production of residues, this considering that the average harvest index was 0.5. The residues generated in the evaluated cropping systems play a determining role in increasing the levels of organic matter, carbon and nutrients. In the scenario where 100 % residue retention was assumed, SOC mineralization fluctuated between 345 and 1 000 kg C·ha-1·year-1 (Figure 3A). In this case, 19 % of the plots were located in the upper part of the bisector, which indicates that the incorporated residue volumes improve the C reserves in the soil. However, even with this management there are challenges, since in most cropping systems the organic reserves and their mineralization in the soil are insufficient with respect to the C contributed by the residues.

In the 50 and 30 % residue retention scenarios (Figures 3B and 3C), it can be seen that the mineralization and contribution of C of the residues tends to be less than the C mineralization of the soil, which contributes to assuming its humic decapitalization, as well as indicating an imbalance between the two C sources. In the 50 % scenario (Figure 3B), C mineralization of residues ranged from 153 to 442 kg C·ha-1 and only one case was in a balance condition. When reducing residue retention to 30 % (Figure 3C), C mineralization showed a greater imbalance, since the difference between C mineralization of the soil and residues was 509 kg C·ha-1. This scenario illustrates the general trend of farming systems in the region, where residues are removed or burned to facilitate soil preparation work.

Several studies have shown that residue retention increases organic matter levels, mainly in regions where they are the only source of organic matter (Fregoso-Tirado, 2008; Flores-Sánchez, Groot, Lantinga, Kropff, & Rossing, 2015; Rusinamhodzi, Wijkc, Corbeels, Rufino, & Giller, 2015). On the other hand, the burning of residues sends carbon emissions into the atmosphere and decapitalizes soil C, although the capture of atmospheric carbon by crops and its incorporation into the soil can mitigate CO2 emissions. In addition, residue burning has reduced soil organic matter levels (from 2.6 to 0.6 %) in the last three decades, and has favored the increase in fertilization doses (Fregoso-Tirado et al., 2002); consequently, soil compaction problems and decreased nutrient efficiency occur. In the regional context, a challenge is to improve soil quality and its efficient technical-economic management.

The incorporation of residues, as well as the efficient application of mineral and organic sources, are strategies that contribute to increasing organic matter and carbon reserves, releasing nutrients (Govaerts et al., 2009), influencing yield and reducing mineral fertilizer needs in the long term (Kamkar, Akbari, Teixeira-da Siliva, & Movahedi-Naeni, 2014). These strategies should be applied through a holistic-integral approach (Liu et al., 2006), as they demand knowledge about local-scale decomposition processes and their potential for regional replication, which is essential for recycling, mineralization, availability of macronutrients and reduction of negative impacts on the environment (Powlson, Whitmore, & Goulding, 2011). These options should be an essential component in strategies aimed at improving the productivity of farming systems, in addition to increasing resilience to climate change (Lal, 2009).

## Conclusions

Nutrition management in maize cropping systems is very diverse among farmers in the region studied (Guanajuato, Mexico). On the one hand, nitrogen acts as a limiting factor as it is in unbalanced conditions, and on the other hand, phosphorus and potassium did not show restrictions in their availability.

The residue management showed that there is a carbon deficit, characterized by the imbalance between the mineralization of soil C and the incorporation of residues. The management of maize nutrition and soil organic matter have not been promoted or adopted as a regional strategy to reduce production costs in the short and medium term, and to improve the physical, chemical and biological properties of the soils.

The regional diagnosis evidences the need for comprehensive studies for the management of fertility and nutrition of the maize cropping systems, with the aim of promoting strategies of mineral and organic management of fertility, contributing to its efficient use, reducing environmental impacts and favoring sustainable management.

## References

Aguado-Lara, G., Etchevers-Barra, J. D., Hidalgo-Moreno, C., Galvis-Spíndola, A., & Aguirre-Gómez, A. (2002). Dinámica del potasio en suelos agrícolas. Agrociencia 36(1), 11-21. Retrieved from https://www.redalyc.org/html/302/30236102/

Alcántar, G., & Sandoval, V. M. (1999). Manual de análisis químico de tejido vegetal. México: Sociedad Mexicana de la Ciencia del Suelo.

Ali, A., Zia, M. S., Hussain, F., Salim, M., Mahmood, I. A., & Shahzad, A. (2005). Efficacy of different methods of potassium fertilizer application on paddy yield, K uptake and agronomic efficiency. Pakistan Journal of Agricultural Sciences, 42(1-2), 27-32. Retrieved from https://www.pakjas.com.pk/papers/455.pdf

Andraski, T. W., Bundy, L. G., & Brye, K. R. (2000). Crop management and corn nitrogen rate effects on nitrate leaching. Journal of Environmental Quality, 29(4), 1095-1103. doi: 10.2134/jeq2000.00472425002900040009x

Báez-Pérez, A., Arreola-Tostado, J. M., Triomphe, B., Bautista-Cruz, A., & Licea-Morales, P. J. (2014). Implementación de la siembra directa para producción de cebada maltera en el estado de Guanajuato. Revista Mexicana de Ciencias Agrícolas, 3(8), 1509-1519. Retrieved from http://www.scielo.org.mx/scielo.php?script=sci_arttext&pid=S2007-09342012000800003

Bremner, J. M. (1965). Inorganic forms of nitrogen. In: Norman, A. G. (Ed.), Methods of soil analysis Part 2 (pp. 1179-1237). USA: Agronomy monograph, ASA.

Bruulsema, T. W., Fixen, P. E., & Snyder, C. S. (2004). Fertilizer nutrient recovery in sustainable cropping systems. Better Crops, 88(4), 15-17. https://www.ipni.net/ppiweb/bcrops.nsf/$webindex/81A4850CE6E9C87085256F380054252B/$file/04-4p15.pdf

Cassman, K. G. (2003). Ecological intensification of agriculture and implications for improved water and nutrient management. USA: Department of Agronomy and Horticulture - University of Nebraska-Lincoln.

Cassman, K. G., Dobermann, A., Sta Cruz, P. C., Gines, G. C., Samson, M. I., Descalsota, J. P., Alcantara, J. M., Dizon, M. A., & Olk, D. C. (1996). Soil organic matter and the indigenous nitrogen supply of intensive irrigated rice systems in the tropics. Plant and Soil, 182(2), 267-287. doi: 10.1007/BF00029058

Cruzate, G. A., & Casas, R. (2003). Balance de nutrientes. Revista Fertilizar INTA, 8, 7-13. http://www.fertilizando.com/articulos/BalanceDeNutrientes.pdf

Cueto-Wong, J. A., Reta-Sánchez, D. G., Figueroa-Viramontes, U., Quiroga-Garza, H. M., Ramos-Rodríguez, A., & Peña-Cabriales, J. J. (2013). Recuperación de nitrógeno aplicado en forma fraccionada en maíz forrajero utilizando 15N. Ingeniería Agrícola y Biosistemas, 5(1), 11-16. doi: 10.5154/r.inagbi.2012.10.009

Doré, T., Makowski, D., Malézieux, E., Munier-Jalain, N., Tchamitchian, M., & Tittonell, P. (2011). Facing up to the paradigm of ecological intensification in agronomy: revisiting methods, concepts and knowledge. European Journal of Agronomy, 34(4), 197-210. doi: 10.1016/j.eja.2011.02.006

Flores-Sánchez, D., Groot, J. C., Lantinga, E. A., Kropff, M. J., & Rossing, W. A. H. (2015). Options to improve family income, labor input and soil organic matter balances by soil management and maize-livestock interactions. Exploration of farm-specific options for a region in Southwest Mexico. Renewable Agriculture and Food Systems, 30(4), 373-391. doi: 10.1017/S1742170514000106

Fregoso-Tirado, L. E. (2008). Cambios en las características químicas y microbiológicas de un vertisol inducidos por sistemas de labranza de conservación. Terra Latinoamericana, 26(2), 161-170. Retrieved from http://www.scielo.org.mx/scielo.php?pid=S0187-57792008000200009&script=sci_arttext

Fregoso-Tirado, L. E., Salinas-García, J. R., Cabrera-Sixto, J. M., Flores, A., Morrison, J. E., & Lepori, W. (2002). Efecto de sistemas de labranza sobre la calidad de vertisoles en El Bajío. México: CENAPROS-INIFAP-SAGARPA.

Ghosh, B. N., Singh, R. J., & Mishra, P. K. (2015). Soil and input management options for increasing nutrient use efficiency. In: Rakshit, A., Singh, H. B., & Sen, A. (Eds.), Nutrient use efficiency: from basics to advances (pp. 17-27). India: Springer. doi: 10.1007/978-81-322-2169-2

Gomiero, T., Pimentel, D., & Paoletti, M. G. (2011). Is there a need for a more sustainable agriculture?. Critical Reviews in Plant Sciences, 30(1-2), 6-23. doi: 10.1080/07352689.2011.553515

Govaerts, B., Verhulst, N., Castellanos-Navarrete, A., Sayre, K. D., Dixon, J., & Dendooven, L. (2009). Conservation agriculture and soil carbon sequestration: between myth and farmer reality. Critical Reviews in Plant Sciences, 28(3), 97-122. doi: 10.1080/07352680902776358

Grageda-Cabrera, O. A., Medina-Cázares, T., Aguilar-Acuña, J. L., Hernández-Martínez, M., Solís-Moya, E., Aguado-Santacruz, G. A., & Peña-Cabriales, J. J. (2004). Pérdidas de nitrógeno por emisión de N2 y N2O: diferentes sistemas de manejo y tres fuentes nitrogenadas. Agrociencia, 38(6), 625-633. Retrieved from https://www.redalyc.org/articulo.oa?id=30238606

Grageda-Cabrera, O. A., Vera-Núñez, J. A., Aguilar-Acuña, J. L., Macías-Rodríguez, L., Aguado-Santacruz, G. A., & Peña-Cabriales, J. J. (2011). Fertilizer dynamics in different tillage and crop rotation systems in a Vertisol in Central Mexico. Nutrient Cycling in Agroecosystems, 89(1), 125-134. doi: 10.1007/s10705-010-9382-4

Henin, S., & Dupuis, M. (1945). Essai de bilan de la matière organique des sols. Annales agronomiques, 5(1), 161-172.

International Assessment of Agricultural Knowledge, Science and Technology for Development (IAASTD). (2009). Agriculture at a crossroads - Global report. Washington, D.C.: Island Press.

Janssen, B. H., Guiking, F. C. T., van der Eijk, D., Smaling, E. M. A., Wolf, J., & van Reuler, H. (1990). A system for quantitative evaluation of the fertility of tropical soils. Geoderma, 46(4), 299-3. doi: 10.1016/0016-7061(90)90021-Z

Jat, M. L., Satyanarayana, T., Majumdar, K., Parihar, C. M., Jat, S. L., Tetarwal, J. P., Jat, R. K., & Saharawat, Y. S. (2013). Fertiliser best management practices for maize systems. Indian Journal of Fertilizers, 9(4), 80-94. Retrieved from http://sap.ipni.net/ipniweb/region/sap.nsf/0/6983574AABE3655085257BC70044C677/\$FILE/Fertiliser%20Best%20Management%20Practices%20for%20maize_2013.pdf

Kamkar, B., Akbari, F., Teixeira-da Siliva, J. A., & Movahedi-Naeni, S. A. (2014). The effect of crop residue on soil nitrogen dynamics and wheat yield. Advances in Plants and Agriculture Research, 1(1), 1-7. doi: 10.15406/apar.2014.01.00004

Lal, R. (2009). Challenges and opportunities in soil organic matter research. European Journal of Soil Science, 60(2), 158-169. doi: 10.1111/j.1365-2389.2008.01114.x

Liu, X., Herbert, S. J., Hashemi, A. M., Zhang, X., & Ding, G. (2006). Effects of agricultural management on soil organic matter and carbon transformation - a review. Plant soil environment, 52(12), 531-543. Retrieved from https://www.agriculturejournals.cz/publicFiles/50927.pdf

Montzka, S. A., Dlugokencky, E. J., & Butler, J. H. (2011). Non-CO2 greenhouse gases and climate change. Nature, 476, 43-50. doi: 10.1038/nature10322

Paredes, R., Alamilla, M. P., & Mandujano, A. (2014). Uso de sensores infrarrojos para estimar dosis de fertilización racional en maíz en Guanajuato. Revista Chapingo Serie Zonas Áridas, 13(1), 3-8. doi: 10.5154/r.rchsza.2012.06.016

Peña-Cabriales, J. J., Grageda-Cabrera, O. A., & Vera-Núñez, J. A. (2001). Manejo de los fertilizantes nitrogenados en México: uso de las técnicas isotópicas (15N). Terra Latinoamericana, 20, 51-56. Retrieved from https://www.redalyc.org/html/573/57320109/

Pérez-Espejo, R., Jara-Durán, K. A., & Santos-Baca, A. (2011). Contaminación agrícola y costos en el Distrito de riego 011, Guanajuato. Revista Mexicana de Ciencias Agrícolas, 2(1), 69-84. Retrieved from http://www.scielo.org.mx/scielo.php?script=sci_arttext&pid=S2007-09342011000700006

Powlson, D. S., Whitmore, A. P., & Goulding, K. W. T. (2011). Soil carbon sequestration to mitigate climate change: a critical re‐examination to identify the true and the false. European Journal of Soil Science, 62(1), 42-55. doi: 10.1111/j.1365-2389.2010.01342.x

Ramírez-Barrientos, C. E., Figueroa-Sandoval, B., Ordaz-Chaparro, V. M., & Volke-Haller, V. H. (2006). Efecto del sistema de labranza cero en un Vertisol. Terra Latinoamericana , 24, 109-118. Retrieved from https://www.redalyc.org/pdf/573/57311494013.pdf

Reddy, P. P. (2015). Climate resilient agriculture for ensuring food security. India: Springer . doi: 10.1007/978-81-322-2199-9_2

Rusinamhodzi, L., Wijkc, T. M., Corbeels, M., Rufino, M. C., & Giller, K. E. (2015). Maize crop residue uses and trade-offs on smallholder crop-livestock farms in Zimbabwe: Economic implications of intensification. Agriculture, Ecosystems and Environment, 214, 31-45. doi: 10.1016/j.agee.2015.08.012

Sattari, S. Z., van Ittersum, M. K., Bouwman, A. F., Smit, A. L., & Janssen, B. H. (2014). Crop yield response to soil fertility and N, P, K inputs in different environments: testing and improving the QUEFTS model. Field Crops Research, 157, 35-46. doi: 10.1016/j.fcr.2013.12.005

Secretaría del Medio Ambiente y Recursos Naturales (SEMARNAT). (2000). Norma Oficial Mexicana NOM-021-RECNAT-2000. México: Author.

Servicio de Información Agroalimentaria y Pesquera (SIAP). (2015). Anuario estadístico de la producción agrícola. Retrieved October 29, 2017, from Retrieved October 29, 2017, from https://nube.siap.gob.mx/cierreagricola/

Smil, V. (2000). Phosphorus in the environment: natural flows and human interferences. Annual Review of Environment and Resources, 25, 53-88. doi: 10.1146/annurev.energy.25.1.53

Soltner, D. (1990). Les bases de la production végétale: Tome 1, Le sol et son amélioration. France: College Science Technology Agriculture.

Vitousek, P. M., Naylor, R., Crews, T., David, M. B., Drinkwater, L. E., Holland, E., …Zhang, F. S. (2009). Nutrient imbalances in agricultural development. Science, 324, 1519-1520. doi: 10.1126/science.1170261

Zhang, F., Niu, J., Zhang, W., Chen, X., Li, C., Yuan, L., & Xie, J. (2010). Potassium nutrition of crops under varied regimes of nitrogen supply. Plant and Soil, 335, 21-34. doi: 10.1007/s11104-010-0323-4

### Tables:

Table 1. Average soil property values of maize cropping systems in Valle de Santiago and Salvatierra, Guanajuato, Mexico.
Municipality Statistic pH OM1 C Nt P
(mg·kg-1)
K
(cmol·kg-1)
CEC
(meq·100 g-1)
(g·kg-1)
Valle de Santiago (n = 55) Average 7.7 34.2 19.8 1.70 21.7 1.8 49.9
SD 0.38 6.2 3.6 0.31 15.9 0.66 7.31
Range 6.7-8.3 19.0-48.0 11.0-27.8 0.9-2.4 5.2-82.5 0.7-4.4 32.5-66.5
Salvatierra (n = 13) Average 7.6 18.3 10.6 0.97 15.9 1.94 38.7
SD 0.32 4.3 2.5 0.24 11.3 0.81 10.7
Range 7.3-8.2 10.8-26.0 6.3-15.1 0.6-1.4 7.7-56.3 0.71-3.6 19.0-50.0
1OM = organic matter; C = carbon; Nt = total nitrogen; P = phosphorus; K = potassium; CEC = cation exchange capacity; SD = standard deviation.