González-Rodríguez, López-Hernández, Ramírez-Lozano, Gómez-Meza, Cantú-Silva, Sarquís-Ramírez, and Mora-Olivo: Litterfall deposition and nutrient return in pine-oak forests and scrublands in northeastern Mexico



Introduction

Litterfall in forest ecosystems is composed by leaves, twigs < 2 cm, flowers, fruits, bark fragments, and other plant parts that have fallen to the forest floor (González-Rodríguez et al., 2008; Celentano et al., 2011; Scoriza et al., 2012; Camargo et al., 2015; López-Hernández et al., 2015). Forest litter acts primarily as a route for the transfer of nutrients from vegetation to the soil and the rate at which forest litter falls ? and subsequently decays ? contribute to the regulation of nutrients, as well as to the maintenance of soil fertility, which is essential for the sustainability of forest systems over extended periods of time (Martín, Gallardo, & Santa-Regina, 1996; Silver, Hall, & González, 2014; Zhang, Yuan, Dong, & Liu, 2014).

Litterfall is a measure of the net primary productivity of a given ecosystem and is strongly correlated with the increase in biomass, tree density and canopy openness; however, it is affected by other environmental constraints (such as rainfall, temperature and potential evapotranspiration), altitude, edaphic conditions, and anthropogenic disturbances (Oelbermann & Gordon, 2000; Prause, Arce, & Angeloni, 2003; Zaldívar-Jiménez, Herrera-Silveira, Coronado-Molina, & Alonzo-Parra, 2004; Pavón, Briones, & Flores-Rivas, 2005; Roig, del Rio, Canellas, & Montero, 2005).

Litterfall input varies widely among forest ecosystems in terms of quantity and quality. In this regard, the inter-annual variation in litterfall production in forest stands constituted by deciduous plant species is directly influenced by the prevailing environmental conditions. In contrast, in forest ecosystems comprised by evergreen species, litterfall is generally less and does not reflect the inter-annual variation in primary productivity, but could be a good proxy for average primary productivity (Bellot et al., 1992; Lebret, Nys, & Forgeard, 2001).

Litterfall is a fundamental process in ecosystem dynamics, it is indicative of ecological yield, and is of vital importance in soil formation and maintenance of soil fertility (Andivia et al., 2010; Nunes & Garcia, 2015). The decomposition of the organic matter contributed by litterfall regulates nutrient and energy patterns in forest ecosystems (Facelli & Pickett, 1991; Chapin, Matson, & Mooney, 2002; Weltzin et al., 2005). In addition, litterfall is the main pathway and linkage for the return of minerals absorbed by plant roots to the soil, especially for macro- (e.g. Ca, Mg, K, N and P) and micro-nutrients (e.g. Cu, Fe, Mn and Zn) (González-Rodríguez et al., 2013).

Furthermore, litterfall not only plays an important role in nutrient cycling, it also produces an organic layer that protects the soil from extreme temperature and moisture changes, prevents soil erosion, it is a source of food and host to multiple and complex microbial communities, it increases organic matter mineralization, improves soil physical and chemical properties, such as soil water availability, infiltration and nutrient absorption in forest ecosystems (Chapin, Matson, & Mooney, 2002; Semwal et al., 2003; Wang et al., 2008). In addition, a number of studies have shown that microbial soil activity is an important determinant of the rate of recycling of plant mineral nutrients between organic and inorganic forms, i.e. between plants and the soil in which they grow (Domínguez, Aira, & Gómez-Brandón, 2009; Celaya-Michel & Castellanos-Villegas, 2011).

Mexico, Brazil, Colombia and Indonesia, represent the most biologically megadiverse countries in the world; in particular, Mexico is also one of the most diverse countries with respect to pine or pine-oak forests, since about 55 Pinus species are found in the country, 85% of which are endemic (Mittermeier & Mittermeier, 1992). Similarly, the Tamaulipan thorn scrub plant ecosystem in Mexico shows a great diversity of trees and shrubs, many of which play an important role in silvopastoral activities, a major socio-economic productivity process in the agricultural system in northeastern Mexico (Foroughbakhch et al., 2009). However, land degradation and ecosystem alteration due to natural or anthropogenic disturbances have altered floristic plant composition and plant stand structure (Jiménez-Pérez et al., 2009), which in turn has affected net primary productivity in forest ecosystems by reducing the number of individuals of many species and consequently, has caused the loss of plant cover and, ultimately, species extinction or, as in other instances, the loss of soil fertility among other factors that alter ecosystem landscape (Vázquez & Orozco, 1996).

Therefore, this region provides an opportunity to investigate litterfall production and nutrient return from forest and native vegetation to the soil in order to gain a better understanding of how to sustain and improve biomass productivity in response to changes in resource availability.

Objectives

The objective of this study was to assess monthly litterfall production and nutrient potential deposition through fallen leaves in three types of forest ecosystems of northeastern Mexico: 1) a pine forest, 2) an ecotone in a transition zone between a pine-oak forest and a piedmont shrubland, and 3) a thorn scrub in the Tamaulipan thorn-scrub vegetation community.

Materials and methods

Study area

The study was carried out at three sites located in the state of Nuevo Leon, Mexico. Site 1 “pine forest” was located at the Experimental Forest Research Station of the Universidad Autónoma de Nuevo Leon, in Iturbide County (24°43'N; 99°52'W; 1600 m a.s.l.). A pine (Pinus pseudostrobus Lindl.) forest mixed with deciduous trees comprises the vegetation community in this location, where soils are mainly rocky lutite or siltstone from the Upper Cretaceous; mean annual air temperature is 13.9 °C and annual rainfall amounts to 639 mm on average. Site 2 “ecotone” was located in the ecotone of a Quercus spp. forest and a Piedmont shrubland (24° 46' N; 99° 41' W; 550 m a.s.l.) in Linares County. Average annual rainfall is approximately 755 mm and annual mean air temperature is 21 °C (González-Rodríguez et al., 2004). Site 3 “thorn scrub” was located at the Experimental Research Station at the Faculty of Forest Sciences of Universidad Autónoma de Nuevo León, also in Linares County (24º 47' N; 99º 32' W; 350 m a.s.l.). The climate is subtropical and semiarid with a warm summer. Annual mean air temperature is 22.3 °C and average total annual precipitation is about 805 mm (González-Rodríguez et al., 2004). The vegetation in site three is known as Tamaulipan thorn scrub or subtropical thorn scrub woodlands (Secretaría de Programación y Presupuesto-Instituto Nacional de Geografía e Informática, 1986). In ecotone and thorn scrub sites, predominant soils are deep, dark-gray, lime-gray, lime-clay Vertisols with montmorillonite, which shrink and swell significantly in response to changes in soil moisture content.

Vegetation of the study area

The main type of vegetation in the three study sites is characterized by trees and shrubs formation, with dominant floristic elements 2 m to 7 m tall, mostly perennial thorny, with small, deciduous leaves. A total of 13 710 individuals belonging to 28 families were registered (Ramírez-Lozano et al., 2013). The density for the pine forest, ecotone, and thorn scrub sites was 3850 individuals per hectare (ind ha-1), 3120, and 3360 ind ha-1, respectively. The sites with the lowest and highest plant cover were the pine forest (14 844 m2 ha-1) and the ecotone (17 712 m2 ha-1). The most frequent species in the pine forest site were Quercus canbyi, Pinus pseudostrobus and Rhus pachyrrachis (with 11.9%); while in the ecotone the most common species was: Havardia pallens (9.9%) and in the thorn scrub Havardia pallens and Forestiera angustifolia (with 9.8%) were the most abundant species. According to the Shannon index, the species richness documented for the pine forest, ecotone and thorn scrub are 1.64, 1.92 and 2.02 (Ramírez-Lozano et al., 2013). The most representative species in each study site are shown in table 1. The floristic description of the three sites has been reported by Ramírez-Lozano et al. (2013).

Table 1

Scientific names and family of identified plant species at each study site.

Pine forest
Scientific name Family
Acacia farnesiana (L.) Willd. Leguminosae
Arbutus xalapensis Kunth Ericaceae
Croton incanus Kunth Euphorbiaceae
Cupressus arizonica Greene Cupressaceae
Juniperus flaccida Schltdl. Cupressaceae
Litsea pringlei Bartlett. Lauraceae
Pinus pseudostrobus Lindl. Pinaceae
Quercus canbyi Trel. Fagaceae
Quercus glaucoides M. Martens & Galeotti Fagaceae
Quercus laceyi Small Fagaceae
Rhus pachyrrhachis Hemsl. Anacardiaceae
Ecotone
Scientific name Family
Acacia farnesiana (L.) Willd. Leguminosae
Acacia rigidula Benth. Leguminosae
Berberis chochoco Schltdl. Berberidaceae
Bernardia myricifolia (Scheele) S. Watson Euphorbiaceae
Celtis pallida Torr. Ulmaceae
Cordia boissieri A. DC. Boraginaceae
Diospyros texana Scheele Ebenaceae
Ebenopsis ebano (Berland.) Barneby & J.W. Grimes Leguminosae
Eysenhardtia polystachya (Ortega) Sarg. Leguminosae
Forestiera angustifolia Torr. Oleaceae
Fraxinus greggii A. Gray Oleaceae
Helietta parvifolia (A. Gray) Benth. Rutaceae
Quercus virginiana Mill. Fagaceae
Thorn scrub
Scientific name Family
Acacia berlandieri Benth. Leguminosae
Acacia rigidula Benth. Leguminosae
Bernardia myricifolia (Scheele) S. Watson Euphorbiaceae
Castela texana (Torr. & A. Gray) Rose Simaroubaceae
Celtis pallida Torr. Ulmaceae
Cercidium macrum I.M. Johnst. Leguminosae
Condalia hookeri M.C. Johnst. Rhamnaceae
Diospyros texana Scheele Ebenaceae
Eysenhardtia polystachya (Ortega) Sarg. Leguminosae
Forestiera angustifolia Torr. Oleaceae
Havardia pallens (Benth.) Britton & Rose Leguminosae
Helietta parvifolia (A. Gray) Benth. Rutaceae
Porlieria angustifolia (Engelm.) A. Gray Zygophyllaceae
Zanthoxylum fagara (L.) Sarg. Rutaceae

Litterfall sampling

Ten litter wooden canisters (1.0 m2) fitted with a nylon net bottom (1 mm mesh size), were randomly placed in an area of about 2500 m2 at each site for litterfall collection. Canister contents were collected at 15-day intervals from January through December of 2009. Monthly litterfall production was quantitated by mixing the two samples taken 15 days apart. Litterfall contents were manually sorted into the following categories: leaves, reproductive structures (flowers, fruits and seeds), twigs, and miscellaneous residues (unidentified materials, fine plant tissue such as bark fragments, pieces of insect bodies or feces). Samples were dried to constant weight at 65 °C. Dry samples were ground in a Thomas Wiley mill (Thomas Scientific Apparatus, Model 3383, Swedesboro, New Jersey, USA) to pass 1.0 mm mesh sieve. The ground material was collected in previously labeled paper bags with corresponding data for subsequent chemical analysis. The leaves were considered as the main component of litterfall and as they were present throughout the study period.

Mineral analysis

Leaf litter samples from each canister were subjected to mineral analysis as follows. Mineral content was estimated by incinerating samples in a muffle oven at 550 °C for five hours. Ashes were digested in a solution containing HCl and HNO3 using the wet digestion technique (Cherney, 2000). Ca (oxide nitrous/acetylene flame), K, Mg, Cu, Fe, Mn, and Zn (air/acetylene flame) content were estimated by atomic absorption spectrophotometry (Varian, Model SpectrAA-200, Mulgrave, Victoria, Australia); P was determined by spectrophotometry (Lambda 1A, Perkin-Elmer, Waltham, Massachusetts, USA) at 880 nm (Association of Official Analytical Chemists [AOAC], 1997). Mineral nutrient deposition at each site was calculated by multiplying leaf litter production of each sampling date by nutrient concentration for the same sampling date and site and adding them over the entire year; added values at each site were used as an estimate of the annual nutrient deposition. Leaf litter annual deposition values for Ca, K, Mg and P were used to estimate the leaf litter nutrient use efficiency (LLNUE) within each site; LLNUE was defined as the ratio of annual litter mass (kg of leaf litter per hectare per year) to annual litter nutrient deposition (kg of leaf nutrient per hectare per year) (Vitousek, 1982; Read & Lawrence, 2003).

Environmental variables

Air temperature (°C) was registered through HOBO sensors (H8 Family, Forestry Suppliers, Inc., Jackson, Mississippi, USA) at each study site every hour. Daily rainfall (mm) was recorded during the experimental period using a HOBO sensor (Fig. 1).

Figure 1

Monthly mean air temperature and rainfall in the study sites.

2448-7597-mb-25-03-e2531514-gf1.png

Statistical analysis

Litterfall deposition data were subjected to one-way analysis of variance (Steel & Torrie, 1980). Normal distribution and homogeneity of variances for each litter constituent and mineral content data were tested using the Kolmogorov-Smirnov, Shapiro-Wilk and Levene tests (Brown & Forsythe, 1974; Steel & Torrie, 1980), all of which provided enough evidence that litterfall and nutrient deposition data were non-normally distributed; therefore, the Kruskal-Wallis non parametric test was employed (Ott, 1993). Since ANOVA did not lend support to the assumption of equality of variances for most sampling dates, differences in litter deposition and nutrient deposition among sites were validated using the Mann-Whitney U non-parametric test with the Bonferroni´s correction method at P = 0.05 (Wackerly, Mendenhall, & Scheaffer, 2002). The SPSS (Statistical Package for the Social Sciences) software package (standard released version 13.0 for Windows, SPSS Inc., Chicago, Illinois, USA) was used for all statistical analyses.

Results

Litterfall production

Total annual litterfall production and its components (leaves, reproductive structures, twigs, and miscellaneous) are shown in table 2. Total annual input varied from 706 g m-2 year-1 in the ecotone to 483 g m-2 year-1 in the pine forest. Leaves represented the main component of total annual litterfall deposition, ranging from 72.7% (thorn scrub) to 66.1% (ecotone). Twigs represented 8.1% (pine forest), 15.7% (ecotone) and 20.8% (thorn scrub) of total litterfall. Reproductive structures (flowers, fruits and seeds) represented 5.5%, 14.5% and 5.5% of total litterfall deposition. Lastly, miscellaneous constituents were 13.4%, 3.5% and 3.4%, respectively, of total litterfall production.

Table 2

Annual deposition of litterfall components, leaf macro-nutrients (Ca, K, Mg, P, and N) and micro-nutrient (Cu, Fe, Mn, and Zn), and leaf macronutrient use efficiency in each site.

Sites Comparison of means
Annual deposition 1) Pine forest
g m -2 year -1
2) Ecotone
g m -2 year -1
3) Thornscrub
g m -2 year -1
Mean ± SEM
g m -2 year -1
1 vs 2 1 vs 3 2 vs 3
Leaves 351.5 ± 24.3 466.8 ± 28.9 337.6 ± 28.9 385.3 ± 18.7 0.014 0.630 0.005
Twigs 39.2 ± 7.6 111.2 ± 11.3 103.4 ± 20.3 84.6 ± 9.8 ˂0.001 0.003 0.393
Reproductive
structures
27.0 ± 6.2 102.7 ± 30.4 37.5 ± 7.4 55.7 ± 12.0 0.008 0.217 0.035
Miscellaneous 65.1 ± 20.2 25.1 ± 3.7 17.1 ± 3.6 35.8 ± 7.7 0.018 ˂0.001 0.105
Total 483.0 ± 42.7 706.0 ± 32.7 495.6 ± 45.2 561.5 ± 29.5 ˂0.001 0.911 0.002
Macronutrient
Ca 3.66 ± 0.35 11.47 ± 1.36 13.45 ± 1.25 9.53 ± 0.99 ˂0.001 ˂0.001 0.352
K 0.98 ± 0.08 3.80 ± 0.38 3.04 ± 0.46 2.61 ± 0.29 ˂0.001 ˂0.001 0.352
Mg 0.48 ± 0.04 1.29 ± 0.14 1.16 ± 0.15 0.98 ± 0.09 ˂0.001 ˂0.001 0.528
N 2.69 ± 0.2 8.29 ± 0.7 7.17 ± 0.6 6.05 ± 0.55 ˂0.001 ˂0.001 0.226
P 0.14 ± 0.01 0.26 ± 0.01 0.23 ± 0.02 0.21 ± 0.01 ˂0.001 0.001 0.481
Micronutrient
Cu 0.94 ± 0.09 2.92 ± 0.3 1.98 ± 0.2 1.9 ± 0.2 ˂0.001 ˂0.001 0.043
Fe 35.15 ± 2.6 61.30 ± 6.4 89.25 ± 14.7 61.9 ± 6.6 0.002 ˂0.001 0.123
Mn 27.70 ± 7.9 71.80 ± 12.8 16.22 ± 2.7 38.5 ± 6.6 0.003 0.314 ˂0.001
Zn 7.55 ± 0.5 7.75 ± 0.8 7.33 ± 1.1 7.5 ± 0.5 0.853 0.630 0.578
Macronutrient Use
Efficiency
Ca 99.2 ± 5.9 43.2 ± 2.8 25.9 ± 1.6 56.1 ± 6.2 ˂0.001 ˂0.001 ˂0.001
K 363.6 ± 15.5 131.3 ± 11.1 124.1 ± 10.6 206.3 ± 21.8 ˂0.001 ˂0.001 0.912
Mg 729.5 ± 24.2 390.5 ± 37.1 308.5 ± 22.7 476.2 ± 37.4 ˂0.001 ˂0.001 0.165
P 2539.0 ± 111.5 1813.8 ± 80.1 1442.5 ± 48.6 1931.8 ± 96.6 ˂0.001 ˂0.001 0.001
N 134.3 ± 6.8 58.6 ± 3.3 47.3 ± 1.1 80.1 ± 7.5 ˂0.001 ˂0.001 0.011

[i] SEM = standard error of the mean. Macronutrient Use Efficiency was calculated as follows: leaves (g m-2 year-1)/ macronutrient in leaves (g m-2 year-1) (Vitousek, 1982).

[ii] Mean comparison is among sites. Significant probabilities (P < 0.008) are shown in boldface according to the Mann Whitney U test with the Bonferroni´s correction. Values represent the mean ± standard error (n = 10).

Monthly leaf litter deposition varied significantly among sites only six months of the year; a similar pattern was observed for reproductive structures, twigs, miscellaneous and total litterfall (Table 3). Monthly litterfall deposition of leaves (Fig. 2a), twigs (Fig. 2b), reproductive structures (Fig. 2c), miscellaneous (Fig. 2d) and total litterfall (Fig. 2e) showed significant differences in most months during the study period. In general, highest litterfall deposition was registered in the ecotone, followed by the thorn scrub and the pine forest. Leaf deposition in the pine forest ranged from 19.6 g m-2 (September) to 49.8 (April) g m-2. Similarly, in the ecotone it ranged between 16.8 g m-2 (June) and 77.6 g m-2 (February), while in the thorn scrub the corresponding values varied from 15.5 g m-2 (July) to 53.2 g m-2 (February) (Fig. 2a). Twig deposition in the pine forest ranged from 0.4 g m-2 (January) to 7.8 g m-2 (January); and in the ecotone it varied from 4.1 g m-2 to 16.3 g m-2 in November and April, respectively. In the thorn scrub twig deposition varied from 2.4 g m-2 in December to 15.5 g m-2 in May (Fig. 2b). In the pine forest, deposition of reproductive structures ranged from 0.5 g m-2 (September) to 6.6 g m-2 (December); in the ecotone it fluctuated between 1.8 g m-2 (January) and 29.0 g m-2 (October), and in the thorn scrub varied from 0.46 g m-2 in January to 7.5 g m-2 in September (Fig. 2c). Miscellaneous deposition in the pine forest ranged from 3.9 g m-2 in February to 7.9 g m-2 in September. In the ecotone varied from 0.4 g m-2 (February) to 9.6 g m-2 (November), while in the thorn scrub it fluctuated from 0.2 g m-2 in December to 6.5 g m-2 in October (Fig. 2d). Total litterfall varied from 28.1 g m-2 (October) to 71.3 g m-2 (April) in the pine forest, from 33.5 g m-2 (July) to 90.6 g m-2 (April) in the ecotone, and from 26.6 g m-2 (December) and 67.8 g m-2 (February) in the thorn scrub (Fig. 2e).

Table 3

Summary of the analyses of the Kruskal-Wallis test to detect significant differences among sites for litterfall components and total month deposition.

Month Statistics Litterfall components Total
Leaves Twigs Reproductive
structures
Miscellaneous
January χ2 11.365 2.217 8.152 18.088 6.366
P value 0.003 0.330 0.017 <0.001 0.041
February χ2 14.627 18.795 8.276 8.968 13.169
P value 0.001 <0.001 0.016 0.011 0.001
March χ2 12.924 14.617 3.120 3.254 13.386
P value 0.002 0.001 0.210 0.196 0.001
April χ2 3.259 10.934 4.679 8.828 6.475
P value 0.196 0.004 0.096 0.012 0.039
May χ2 6.320 14.480 1.210 1.866 0.302
P value 0.042 0.001 0.546 0.393 0.860
June χ2 5.437 12.364 9.084 15.347 1.208
P value 0.066 0.002 0.011 <0.001 0.547
July χ2 5.128 13.272 9.246 9.363 6.968
P value 0.077 0.001 0.010 0.009 0.031
August χ2 3.595 18.126 4.121 9.298 4.880
P value 0.166 <0.001 0.127 0.010 0.087
September χ2 8.508 11.948 12.212 10.098 8.578
P value 0.014 0.003 0.002 0.006 0.014
October χ2 3.285 12.364 6.227 1.350 8.434
P value 0.193 0.002 0.044 0.509 0.015
November χ2 2.519 3.468 5.151 11.399 3.089
P value 0.284 0.177 0.076 0.003 0.213
December χ2 7.992 10.426 4.495 16.237 8.849
P value 0.018 0.005 0.106 <0.001 0.012

[i] P values in boldface (P < 0.05) indicate significant differences among sites (per month).

Figure 2

Monthly total nutrient deposition of leaves (a), reproductive structures (b), twigs (c), miscellaneous (d) and total litterfall (e) at research sites.

2448-7597-mb-25-03-e2531514-gf2.png

P-values of the Kruskal-Wallis test to detect significant differences among sites are shown at each sampling month within the graph (* = P ≤ 0.05; ** = P ≤ 0.01; *** = P ≤ 0.001). Plotted values represent the mean ± standard error (n = 10).

Nutrient deposition

Monthly leaf-litter potential nutrient deposition, including Ca, K, Mg, P and N was significantly different among sampling sites (Table 4). In most months during the study, macronutrient (Ca, Mg, N, K and P) deposition via leaf litter was significantly higher in the ecotone site, followed by the thorn scrub and pine forest sites (Fig. 3 a,b,c,d,e). In general, macronutrient deposition was higher during the winter months (January to march) than at any other time of the year. Annual Ca deposition was significantly higher in the thorn scrub compared to other sites, but annual K, Mg, N and P deposition was significantly higher in the ecotone, compared to the other sites (Table 2). Leaf macronutrient deposition in all sites ranked as follows: Ca > N > K > Mg > P. Total annual macronutrient deposition (N + Ca + Mg + K+ P) in the pine forest, ecotone and thorn scrub sites amounted to 8.0, 25.1 and 25.1 g m-2 year-1, respectively. Leaf litter nutrient use efficiency (LLNUE) for Ca, Mg, K, N and P ranked as follows: pine forest > ecotone > thorn scrub. Calcium LLNUE ranged from 25 to 99, potassium from 124 to 363, magnesium from 308 to 729, phosphorus from 1442 to 2539 and nitrogen from 47 to 134 for thorn scrub and pine forest, respectively. Across sites, LLNUE was higher for P followed by Mg, K, N, while it was lowest for Ca (Table 2).

Table 4

Summary of the Kruskal-Wallis test to detect significant differences among sites for macro- (Ca, K, Mg, P and N) and micronutrient (Cu, Fe, Mn, and Zn) deposition.

Month Nutrient
Statistic Ca K Mg P N Cu Fe Mn Zn
January χ2 19.935 18.449 18.243 10.888 15.719 16.717 14.356 13.427 5.084
P value <0.001 <0.001 <0.001 0.004 <0.001 <0.001 0.001 0.001 0.079
February χ2 17.701 19.425 13.985 15.564 14.999 15.246 13.350 11.365 2.108
P value <0.001 <0.001 0.001 <0.001 0.001 <0.001 0.001 0.003 0.348
March χ2 19.419 20.286 17.654 15.037 20.101 19.173 14.759 8.988 2.821
P value <0.001 <0.001 <0.001 0.001 <0.001 <0.001 0.001 0.011 0.244
April χ2 11.430 7.357 7.404 5.739 11.530 10.738 1.866 13.915 5.739
P value 0.003 0.025 0.025 0.057 0.003 0.005 0.393 0.001 0.057
May χ2 5.004 6.730 0.705 0.405 4.137 1.425 3.177 9.014 6.676
P value 0.082 0.035 0.703 0.817 0.126 0.490 0.204 0.011 0.036
June χ2 4.710 3.479 0.379 0.163 1.373 5.978 1.644 6.604 4.408
P value 0.095 0.176 0.827 0.922 0.503 0.050 0.440 0.037 0.110
July χ2 11.166 14.524 13.195 9.742 13.990 16.297 2.563 18.356 4.137
P value 0.004 0.001 0.001 0.008 0.001 <0.001 0.278 <0.001 0.126
August χ2 12.480 17.290 12.560 4.160 13.822 14.835 2.728 15.120 7.310
P value 0.002 <0.001 0.002 0.125 0.001 0.001 0.256 0.001 0.026
September χ2 18.289 19.094 19.636 18.774 19.295 21.311 17.861 21.154 5.345
P value <0.001 <0.001 <0.001 <0.001 <0.001 <0.001 <0.001 <0.001 0.069
October χ2 12.294 7.837 9.726 10.640 14.895 4.319 8.991 5.236 6.434
P value 0.002 0.020 0.008 0.005 0.001 0.115 0.011 0.073 0.040
November χ2 4.253 4.483 1.435 0.147 4.865 2.290 1.241 8.226 2.387
P value 0.119 0.106 0.488 0.929 0.088 0.318 0.538 0.016 0.303
December χ2 4.601 0.095 0.134 1.427 4.028 2.775 3.585 4.625 7.649
P value 0.100 0.953 0.935 0.490 0.133 0.250 0.167 0.099 0.022

[i] P values in boldface (P < 0.05) indicate significant differences among sites for the deposition of macro- and micronutrients in the three sites of study.

Figure 3

Monthly deposition of Ca (a), Mg (b), N (c), K (d) and P (e) through leaf litter at research sites.

2448-7597-mb-25-03-e2531514-gf3.png

P-values of the Kruskal-Wallis test to detect significant differences among sites are shown at each sampling month within the graph (* = P ≤ 0.05; ** = P ≤ 0.01; *** = P ≤ 0.001). Plotted values represent the mean ± standard error (n = 10).

Leaf-litter potential micronutrient (Cu, Fe, Mn, and Zn) deposition was significantly different among sites, particularly in winter (Table 4). Potential Cu, Fe, Mn, and Zn deposition through fallen leaves (Fig. 4 a,b,c,d) was significantly different in most months, being higher in the ecotone site followed by the thorn scrub and pine forest. In general, micronutrient deposition was higher in winter, when leaf litter deposition was also higher than in any other season (Fig. 2a). The annual potential deposition of Cu, Fe and Mn was significantly higher in the ecotone than in the pine forest or the thorn scrub (Table 2). However, potential deposition of leaf Zn was not different (P > 0.05) among sites. Leaf micronutrient deposition ranked as follows: Fe > Mn > Zn > Cu (Table 2). Total annual micronutrient deposition (Cu + Mn + Fe + Zn) was 143.7 mg m-2 year-1, 114.8 mg m-2 year-1 and 71.3 mg m-2 year-1 for the ecotone, thorn scrub and pine forest, respectively.

Figure 4

Monthly deposition of Cu (a), Fe (b), Mn (c), and Zn (d) through leaf litter at research sites.

2448-7597-mb-25-03-e2531514-gf4.png

P-values of the Kruskal-Wallis test to detect significant differences among sites are shown at each sampling month within the graph (* = P ≤ 0.05; ** = P ≤ 0.01; *** = P ≤ 0.001). Plotted values represent the mean ± standard error (n=10).

Discussion

Litterfall

The highest and lowest total annual litterfall measurements were recorded in the ecotone and the pine forest, respectively. A similar trend was observed for twigs and reproductive structures; in contrast, miscellaneous depositions were higher at the Pinus forest plant community (Table 2). These observations are similar to litterfall values previously reported in studies conducted in the same region (López-Hernández et al., 2013) and in the microphyllous desert scrubland at northeastern Mexico (González-Rodríguez et al., 2013); however, lower quantities (202.7 g m-2 year-1, 100.2 g m-2 year-1 and 35.2 g m-2 year-1) were recorded by Martínez-Yrizar, Nuñez, Miranda, and Búrquez (1999) in the Sonora Desert vegetation of northern Mexico. In this study, leaves represented the major component of litterfall; 66% to 72%. These percentages are within the ranges reported by González-Rodríguez et al. (2011), González-Rodríguez et al. (2013) and López-Hernández et al. (2015) for these ecosystems. Santa-Regina (2000), Santa-Regina and Tarazona (2001) and Caritat, García, Lapeña, and Vilar (2006) reported that the leaf component represented 50% to 80% of all litterfall in pine and pine-oak forests. Apparently, the amount of leaves produced with respect to the total plant biomass that falls on the ground becomes subject to mineralization processes that eventually recycle nutrients present in dead plant tissues back into the soil and could depend on the stage of development and age of the plant. Maximum contribution to forest litter seems to occur concomitantly with highest rates of carbon assimilation and respiration during periods of high litterfall production (Martínez-Alonso et al., 2007). Moreover, the observed differences in leaf fall at the ecotone ecosystem, relative to the Pinus forest ecosystem, could relate to the continuous shedding of leaves by abundant deciduous plant species in the first case. A much studied morpho-physiological adaptive mechanism in plants of the Tamaulipan thorn scrub ecosystem to cope with severe water deficit and high temperature, and thus prevent excessive water loss through transpirational flux and extreme plant tissue dehydration, could relate to litterfall deposition (González-Rodríguez et al., 2004).

The differences in production and composition of litterfall among sites may be due to variations in plant species composition of the vegetation community at each site (Table 1), as this clearly reflects diverse plant phenology patterns. The pine forest was a mixed forest plant community comprised of pine trees (Pinus pseudostrobus Lindl.) and several deciduous trees. At the ecotone site, the vegetation is constituted by Quercus spp. and diverse species of the Piedmont shrubland, while in the thorn scrub, the vegetation corresponds to the Tamaulipan thorn scrub or subtropical thorn scrub woodlands. In addition, prevailing climatic conditions registered at each study area influenced litterfall deposition; in general, higher litterfall deposition occurred in the months with lower rainfall and lower temperatures (Fig. 1).

Similar to the findings reported herein, several researchers have reported that litter production in forest ecosystems is determined by climatic conditions, species composition, and successional stage (Haase, 1999; Sundarapandian & Swamy, 1999; González-Rodríguez et al., 2013; López-Hernández et al., 2015). Similar responses were reported by González-Rodríguez et al. (2013) and López-Hernández et al. (2013) in studies carried out in microphyllous vegetation and in a thorn scrub, respectively. In agreement with our findings, Bellot et al. (1992), Lebret, Nys, and Forgeard (2001). Caritat, García, Lapeña, and Vilar (2006) and Martinez-Alonso et al. (2007) reported that the dynamics of productivity of aerial biomass it is very dependent on the variability of climatic conditions between different years; therefore, it is difficult to establish a general pattern of litterfall production and composition in short periods, in areas with great climatic variability.

Mineral deposition

Regardless of location, deposition of macronutrients through litterfall occurred in the following order: Ca > N > K > Mg > P. Similar values have been reported for the Tamaulipan thorn scrub vegetation (González-Rodríguez et al., 2011; López-Hernández et al., 2013), for a microphyllous desert vegetation, (González-Rodríguez et al., 2013), for a wet forest community in Colombia (Del Valle-Arango, 2003), for a natural forest in subtropical China (Yang, Wang, Kellomäki, & Zhang, 2006), and for legume agroforestry species (Sileshi & Mafongoya, 2007). The deposition of micronutrients through litterfall observed in this study (Fe > Mn > Zn > Cu) was similar to those reported by González-Rodríguez et al. (2013) and López-Hernández et al. (2013) in studies carried in microphyllous vegetation and in a thorn scrub in northeastern Mexico, respectively, and by Andivia et al. (2010) in a Quercus suber vegetation in the Mediterranean region in Spain.

In the present study, macronutrient use efficiency was significantly higher at the pine forest than at the other sites. In this regard, it is tempting to speculate that woody plant species from the pine forest could be more efficient in nutrient translocation than plant species from the other sites, since annual deposition levels of Ca, K, Mg, P y N, observed in leaf litter from the pine forest were lower compared with the ecotone and thorn scrub sites (Table 2). Although P deposition via leaf litterfall was lower than for other macronutrients, its nutrient use efficiency was relatively higher than that for Ca, N, K or Mg. A similar pattern has been previously documented in different ecosystems (Del Valle-Arango, 2003; Swamy, Kushwaha, & Puri, 2004; Safou-Matondo, Deleporte, Laclau, & Bouillet, 2005; González-Rodríguez et al., 2011; López-Hernández et al., 2013). It has been argued that P maybe translocated to other plant structures before leaf senescence to participate in the development of new plant structures or physiological processes (Palma et al., 2000).

In contrast, the low levels of N in the pine forest, compared with the ecotone or the thorn scrub, could be associated with the capability of symbiotic nitrogen fixation of leguminous plant species observed at the study sites, since at the pine forest, plant species belonging to the Leguminosae family represented only 4% of total species richness, while in the ecotone and thorn scrub sites, leguminous species represented about 20% and 25%, of the vegetation community, respectively. Therefore, the efficiency in N use from litterfall was determined by the presence of legume plant species at the study sites. This agrees with Rothe and Binkley (2001) and Forrester, Bauhus, and Cowie (2005), who reported that in mixed forest stands, N-fixing species increased and improved nutrient cycling through litterfall relative to stands containing fewer N-fixing species.

In general, higher deposition of leaves (winter months) coincided with higher potential in nutrient deposition in the three study sites. In addition, higher rainfall at the ecotone and thorn scrub during the study period (Fig. 1) may be involved in the increase of nutrient deposition in those sites, as compared to the pine forest (Ramírez-Lozano et al., 2013). Increase in mineral contents due to higher rainfall has also previously reported by Ramírez-Lozano et al. (2010), who evaluated the mineral profile of native shrubs in northeastern Mexico.

Although in this study, nutrient content and deposition were not measured in other litter constituents such as twigs or reproductive structures, other studies have demonstrated that the nutrient content can be higher in other components than in leaves (Cantú-Silva et al., 2013) but with lower annual depositions.

Conclusions

This research aimed to contribute to our understanding of the role played by seasonal mineral nutrient cycling from litterfall back to the soil in support of the sustainability at three different forest ecosystems: a Pinus forest (Pine forest), a Quercus forest and the Piedmont thorn scrub (Ecotone) and a Tamaulipan thorn scrub woodland (Thorn scrub). Deposition of litterfall and its components varied among both, sites and months. The ecotone registered the highest total deposition, followed by the thorn scrub and the pine forest. Winter months showed the highest deposition during the year. Deposition of leaves was highest, followed by twigs and reproductive structures, while miscellaneous was the lowest proportion of total litterfall regardless of site. In general, leaf Ca was deposited to larger amounts, followed by N, K, Mg and P. The P deposition in leaves had higher nutrient use efficiency than other macronutrients. Differences in potential for nutrient cycling to the soil may relate to differences among sites with respect to climate, plant composition of vegetation communities, litterfall nutrient composition and soil microbial activity. Since study has been conducted for one year, intern-annual variation in litterfall production and nutrient returns should be considered.

Acknowledgements

We gratefully acknowledge technical assistance provided by Elsa Dolores González Serna and Manuel Hernández Charles. The authors also appreciate and acknowledge the landowner of the ecotone site for providing the necessary assistance to establish the experimental plot. We wish to thank two anonymous referees for critical reading of our manuscript and for their constructive comments, which helped to improve the manuscript. This research was partially funded by Universidad Autónoma de Nuevo León (PAICYT, grant CT259-15) and by the Consejo Nacional de Ciencia y Tecnología (CONACYT, grant 250732).

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Notes

[5] This paper must be cited as:
González-Rodríguez, H., López-Hernández, J. M., Ramírez-Lozano, R. G., Gómez-Meza, M., V., Cantú-Silva, I., Sarquís-Ramírez, J. I., & Mora-Olivo, A. (2019) Litterfall deposition and nutrient return in pine-oak forests and scrublands in northeastern Mexico. Madera y Bosques, 25(3), e2531514. doi: 10.21829/myb.2019.2531514



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Madera y Bosques, Vol. 26, Núm. 2, Verano2020, es una publicación cuatrimestral editada por el Instituto de Ecología, A.C. Carretera antigua a Coatepec, 351, Col. El Haya, Xalapa, Ver. C.P. 91070, Tel. (228) 842-1835, http://myb.ojs.inecol.mx/, madera.bosques@inecol.mx. Editor responsable: Raymundo Dávalos Sotelo. Reserva de Derechos al Uso Exclusivo 04-2016-062312190600-203, ISSN electrónico 2448-7597, ambos otorgados por el Instituto Nacional del Derecho de Autor. Responsable de la última actualización de este Número, Reyna Paula Zárate Morales, Carretera antigua a Coatepec, 351, Col. El Haya, Xalapa, Ver., C.P. 91070, fecha de última modificación, 12 de mayo de 2020.

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