Revista Mexicana de Ciencias Forestales Vol. 14 (77)

Mayo – Junio (2023)

Fecha de recepción/Reception date: 26 de octubre de 2022

Fecha de aceptación/Acceptance date: 15 de marzo de 2023

_______________________________

¹Programa BEMARENA, Universidad de Guadalajara

²Departamento Forestal, Universidad de Guadalajara

³Facultad de Ciencias Forestales, Instituto Tecnológico de El Salto

⁴Departamento de Ecología, Universidad de Guadalajara

⁵Postgrado en Ciencias Forestales, Colegio de Postgraduados

⁶Tecnológico Nacional de México

*Autor para correspondencia; correo-e: eduardo.salcedo@academicos.udg.mx

*Corresponding author; e-mail: eduardo.salcedo@academicos.udg.mx

Abstract

The Flora and Fauna Protection Areas Bosque La Primavera (BLP) and Sierra de Quila (SQ) in the state of Jalisco, are frequently affected by anthropic factors that modify their spatial distribution and tree growth. The objective of this study was to compare basal area, stem density and annual periodic increment in basimetric area for type of vegetation in both natural protected areas in the 2005-2020 period. In both areas, were measured the normal diameter (nd) and total height of trees in 88 sampling plots, established in 2005 and remeasured in 2013 and 2020. The mean basimetric area of BLP was 13, 12 and 16 m² ha^-1 (2005, 2013 and 2020, respectively), with a mean increment of 0.21 m² ha^-1 year^-1; while in SQ it was 16, 18 and 20 m² ha^-1 (for 2005, 2013 and 2020, respectively) with an increment of 0.27 m² ha^-1 year^-1. The most representative diameter categories for the dominant species were 10 to 15 cm of nd for Quercus magnoliifolia in BLP, Quercus resinosa and Pinus douglasiana in SQ, and 20 to 25 cm of nd for Pinus oocarpa in BLP. Stem density, basal area and the annual periodic increment was higher in SQ than in BLP, attributable to the forest fires that affected BLP every year, despite that in SQ sanitation fellings were made to control bark beetle outbreaks and mistletoe infestations.

Key words: Bosque La Primavera, oak–pine forest, diameter categories, stem density, periodic annual increment, Sierra de Quila. 

Resumen

Las áreas de protección de flora y fauna Bosque La Primavera (BLP) y Sierra de Quila (SQ) del estado de Jalisco son afectadas con frecuencia por factores antrópicos que modifican la distribución espacial y crecimiento de las especies arbóreas. El objetivo del presente estudio fue comparar el área basal, la densidad de árboles y el incremento periódico anual en área basal por tipo de vegetación en ambas áreas naturales protegidas durante el periodo 2005-2020. En las dos áreas, se midieron el diámetro normal (dn) y la altura total de los árboles en 88 sitios de muestreo, establecidos en 2005 y remedidos en 2013 y 2020. El área basal promedio del BLP fue de 13, 12 y 16 m² ha^-1 para 2005, 2013 y 2020, respectivamente, con un incremento promedio de 0.21 m² ha^-1 año^-1; mientras que en SQ fue de 16, 18 y 20 m² ha^-1 para 2005, 2013 y 2020, con un incremento promedio de 0.27 m² ha^-1 año^-1. Las categorías diamétricas más representativas para las especies dominantes fueron 10 a 15 cm de dn para Quercus magnoliifolia en BLP, Quercus resinosa y Pinus douglasiana en SQ, y 20 a 25 cm de dn para Pinus oocarpa en BLP. La densidad, el área basal y el incremento periódico anual en área basal fueron mayores en SQ, atribuible a los incendios que afectan cada año al BLP, a pesar de que en SQ se hicieron cortas de saneamiento por ataque de plagas e infestaciones por muérdago.

Palabras clave: Bosque La Primavera, bosques de encino-pino, categorías diamétricas, densidad, incremento periódico anual, Sierra de Quila.

Introduction

Protected Natural Areas (ANP, for its acronym in Spanish) frequently have land tenure problems (González et al., 2014), lack of resources and invasion (Maldonado et al., 2020). In addition, they do not have management programs or they are not applied (Maldonado et al., 2020). This has caused the risk of disturbance factors such as droughts, diseases and pests, to increase the vulnerability of wooded areas to those caused by man such as fires and land use change (González et al., 2014).

In the state of Jalisco, the Bosque La Primavera (BLP, for its acronym in Spanish) Flora and Fauna Protection Area (APFF, for its acronym in Spanish) provides environmental services such as aquifer recharge, carbon capture and recreation from its proximity to the Guadalajara Metropolitan Area (ZMG, for its acronym in Spanish) (Balderas and Lovett, 2013). In this APFF, there is the forest management program published in the Official Gazette of the Federation in 1984, however, only protection activities are carried out (Álvarez, 2016).

On the other hand, the Sierra de Quila (SQ, for its acronym in Spanish) APFF is located 100 km from the ZMG. Despite having been decreed in 1982, it still does not have a published management program up to now, so only protection activities are carried out (Conanp, 2022). In addition, the impact of natural and anthropic disturbances on the forest communities of both APFFs is quantitatively unknown.

One way to assess the impact of natural and anthropic disturbances on forests is through structural and growth analysis of tree stands using quantitative (Aguirre et al., 2003) and dynamic analysis of changes in parameters such as basimetric area (AB) and the density of trees.

More than 208 thousand people attend the BLP annually according to the visitor registry of the Bosque La Primavera Decentralized Public Organization (OPD) for the year 2021, who carry out recreational activities such as camping, cycling and hiking. In the case of SQ, the annual visitors are around 7 thousand (OPD Sierra de Quila visitor record for the year 2021) and recreational activities are also carried out.

Another factor that distinguishes these two APFFs is land tenure, since while in SQ there are eight ejidos, one indigenous community and 10 small properties, in BLP 50 % of the area belongs to small owners who mostly own fenced off their properties (Álvarez, 2016).

This suggests a differential human pressure in both APFF. Although both in BLP and in SQ, human activity generates contamination of the riverbeds, scattered garbage, and damage to the vegetation (Álvarez, 2016), the deterioration can be more severe in BLP, where the influx of visitors is greater and shorter he distance to the urban area.

Therefore, the objective of this work was to compare the basimetric area, tree density and the increase in the basimetric area by type of vegetation in both natural protected areas in the 2005-2020 period under the following hypothesis: The proximity to the ZMG of the Bosque La Primavera APFF causes a greater negative effect on the structure and development of the trees compared to the Sierra de Quila APFF, which presents less anthropic pressure.

Materials and Methods

Study area

Field work was carried out in Bosque La Primavera (BLP) and Sierra de Quila (SQ) Flora and Fauna Protection Areas (APFF) in the state of Jalisco. BLP is located in the Sierra La Primavera, west of the Guadalajara city metropolitan area (Figure 1). It was decreed on March 6, 1980 with 30 500 ha, between 20º32' to 20º44' N and 103º28' to 103º42' W. Its altitudinal range is 1 400 to 2 200 m, in Tala, Zapopan and Tlajomulco municipalities, Jalisco. The predominant climate is temperate sub-humid and semi-warm sub-humid (García, 2004). The average annual precipitation fluctuates between 800 and 1 000 mm, and the average annual temperature is 20 °C. The predominant type of vegetation is mixed pine-oak or oak-pine forests, although there are also areas of gallery forest and low deciduous forest (Gallegos et al., 2014).

Figure 1. Location of Bosque La Primavera and Sierra de Quila Flora and Fauna Protection Areas.

The Sierra de Quila APFF was decreed on August 4^th, 1982 with 15 192 hectares in Tecolotlán, Tenamaxtlán, San Martín Hidalgo and Cocula municipalities, Jalisco (Figure 1). It is located between 20º14' to 20º21' N and 103º57' to 104º07' W. The altitude ranges between 1 350 and 2 560 m. The climate is humid temperate, with average annual temperature between 12 and 18 °C; average annual rainfall is 900 mm. The types of vegetation reported are mainly oak-pine forest, oak forest, gallery forest and low deciduous forest (Villavicencio et al., 2012).

In both APFF, according to González-Abraham et al. (2015) the vegetation cover is in good environmental conditions. The zoning of the BLP according to the forest management program published in the Diario Oficial de la Federación (DOF, for its acronym in Spanish) (Official Gazette of the Federation) (Semarnat, 2001) is agroecosystems, sustainable use of natural resources, special use, protection, recovery, public use and restricted use while in SQ it is sustainable use of ecosystems, preservation, public use and recovery, however, the management program is not published in the DOF.

Field data

The BLP used information from 37 permanent sites the 400 m² established for National Forest and Soil Inventory (Infys, for its acronym in Spanish), whose first measurement was carried out in 2005, and the second in 2013 (Conafor, 2019). In addition, data from 20 permanent sites 1000 m² established in 2005 were used to define indicators for BLP restoration after fire. In the SQ, the information was collected in 31 permanent sites established for the Infys, where the first and second measurements were made in the same years previously mentioned.

A stratified sampling design was used. The types of vegetation were the strata oak forest (OF), pine forest (PF), mixed pine-oak forest (MPOF), mixed oak-pine forest (MOPF) and seasonaliy dry tropical forest (SDTF). All sites were remeasured in 2020.

The vegetation types considered in this study were defined based on the basal area calculated from the 2020 inventory data, also using the Rzedowski (2006) classification of vegetation types and the Lamprecht mixing ratio (Alvis, 2009).

For the collection of field information in 2020, the center was located with a Garmín eTrex 10 GPS and the site was delimited according to the surface. At each site, the normal diameter (dn, for its acronym in Spanish) (1.30 m above the soil surface) was measured with a 283D Forestry Suppliers cloth diametric tape, and the total height with a 360PC/360R Suunto tandem clinometer of all individuals with dn≥7 cm. With the dn data, the individual basimetric area (BA) was calculated.

Sampling sites

From the field data, the types of vegetation that are mostly shared by both APFFs were determined. In each type of vegetation, the number of sampling sites was different (Table 1), since the Infys conglomerates were based on the total area.

Table 1. Permanent sites by types of vegetation.

No natural areas with forests dominated by pine species were found in the SQ APFF, which coincides with what was recorded by Villavicencio et al. (2012) and Flores et al. (2013).

Tree vegetation structure

To analyze the horizontal structure, frequency histograms were used in which the diameter category was assigned to each 5 cm of normal diameter for the tree species of each APFF.

Increase in basimetric area

Forest growth for each APFF was determined by considering the annual periodic increase (IPA, for its acronym in Spanish) in basimetric area as an indicator. From the remeasured data of the trees in the years 2005, 2013 and 2020, it was determined as the difference of the average estimate per hectare in the year 2020 minus the average of the reference year (2005 and 2013) divided by the number of years in the period by type of vegetation.

Data analysis

With the field data, the average per site, hectare and type of vegetation was obtained. The Shapiro-Wilks (Flores y Flores, 2021) normality test and the Levene variance homogeneity test (Bisquerra, 1987) were applied.

Using a mixed linear model under the repeated measures approach, the relationship between the dependent variables basimetric area, tree density and periodic annual increase in basimetric area was established, with the factors year of measurement, natural protected area and type of vegetation. Since in some cases the sampling sites are contained in a conglomerate, the use of mixed linear models with random intercept was decided. The structure of the model was:

(1)

Where:

Analyzes were performed with SIGMA PLOT software 12.0 version (Systat Software Inc., 2012) and R software 4.1.1 version (R Core Team, 2020).

Results

Diametric structure

In BLP, the species with the largest basimetric area were Quercus magnoliifolia Née, Q. resinosa Liebm. and Pinus oocarpa Schiede ex Schltdl., while for SQ were Q. resinosa, Q. rugosa Née and P. douglasiana Martínez. Values up to 60 cm dn are recorded for all species, except for P. oocarpa and P. douglasiana with individuals up to 80 cm dn.

Quercus magnoliifolia and Q. resinosa in BLP, as well as Q. rugosa and Q. resinosa in SQ showed an inverted J-shaped diametric structure; the 10-15 cm diameter category gathered the largest number of individuals (Figure 2a, b, d, f).

a) Quercus magnolifolia Née, b) Q. resinosa Liebm. and c) Pinus oocarpa Schiede ex Schltdl. in Bosque La Primavera; d) Q. resinosa, e) P. douglasiana Martínez and f) Q. rugosa Née in Sierra de Quila.

Figure 2. Number of trees by diameter category for the species indicated in the two APFF.

In the case of P. oocarpa in BLP, the diameter category with the most individuals went from 10-15 cm in the years 2005 and 2013 to the 25-30 cm class in 2020 (Figure 2c). This trend coincided with a decrease in the number of individuals of the diameter category 10-15 from 1 310 individuals ha^-1 in 2013 to 960 individuals ha^-1 in 2020. P. douglasiana in SQ had a dispersed structure due to the fact that there is a decrease of individuals for the diameter categories 15-20, 25-30 and 30-35 cm dn in the different periods (Figure 2e).

Generalized mixed linear models

The coefficients of the models with random intercept for the variables basimetric area, tree density and periodic increase in basimetric area are shown in Table 2. Most of the estimated parameters are significant (p≤0.05) for tree density. In contrast, only half of the parameters were significant for basimetric area and IPA.

Table 2. Estimated parameters for the dependent variables tree density, basimetric area and IPA in basimetric area.

ANP = Protected Natural Area; TV MOPF = Mixed oak-pine forest type of vegetation; TV MPOF = Mixed pine-oak forest type of vegetation; TV PF = Pine forest type of vegetation; TV SDTF = Seasonaliy dry tropical forest type of vegetation; IPA = Annual Periodic Increase. *significance α<0.05, ** significance α< 0.01.

Tree density

In general terms, tree density was higher in SQ than in BLP throughout the study period. Between periods, the OF and PF of the BLP kept their density constant, since they did not show significant differences between years, which did occur in the MOPF and MPOF, which registered a decrease in density (Table 3).

Table 3. Average density by type of vegetation per sampling year in the Bosque La Primavera (BLP) and in Sierra de Quila (SQ).

There are no significant differences in density throughout the study period. A high variability was detected in this criterion in the two APFF, since there are significant differences between them (p<0.034) and between the types of vegetation with the exception of the MOPF (Table 3).

Increase in BA

BA increased from 2005 to 2020 in both BLP and SQ. Such increment is greater in SQ (p<0.001) except for the MOPF in 2005, where it is greater in BLP (Table 4).

Table 4. Average basimetric area (m² ha^-1) per type of vegetation and measurement years in Bosque La Primavera (BLP) and Sierra de Quila (SQ).

BA increased from 2005 to 2020, and significant differences were detected between periods (p<0.000). While between types of vegetation there were significant differences in SDTF (p<0.000), which registers BA losses in 2020 in SQ, but not for the rest of the types of vegetation.

BA in SQ increased in the same period in all types of vegetation, with the exception of OF and SDTF that had a decrease of 0.60 and 0.90 m² ha^-1, respectively (Table 4).

BA in BLP went from 13 to 16 m² ha^-1, with an increase in the 15-year period of 3 m² ha^-1, while in SQ, it increased from 16 to 20 m² ha^-1, that is, 4 m² ha^-1.

The average increase in BA in the years considered is greater in SQ than in BLP, which is a significant difference (p<0.000); however, from 2013 to 2020, it is higher in BLP than in SQ (Table 5).

Table 5. Increase in basimetric area in the 2005 to 2020 period by type of vegetation in Bosque La Primavera (BLP) and Sierra de Quila (SQ) Flora and Fauna Protection Areas.

When the increase in BA by type of vegetation is analyzed, the periodic annual increase in basimetric area (IPA) is greater in BLP than SQ for OF and SDTF in the periods analyzed, but in mixed forests it is greater in SQ than in BLP (Table 5). In both APFF there are years in which there is a loss of BA, the most evident of which is from 2005 to 2013 (Table 5).

IPA in BLP went from having a negative trend in the 2005 to 2013 period to 0.54 m² ha^-1 year^-1 from 2013 to 2020, which is a significant growth of the forest mass (p<0.001). There is evidence that in BLP the IPA was continuous throughout the study times. In contrast, in SQ IPA decreased between 2005 and 2020, except for the BMPE. However, it is noteworthy that in the SBC, IPA is negative throughout the time of interest (Table 5). When comparing IPA between types of vegetation in each APFF, no significant differences were recorded between periods (Table 1).

Discussion

Diametric structure

Quercus resinosa, Q. magnoliifolia, Q. rugosa and Pinus oocarpa showed an inverted J diametric structure in both APFF, which in a way indicates that the tree community has constant recruitment (Chávez-Flores et al., 2020). Castañeda-González et al. (2012) reported for the BLP in 2012 that the 15-20 cm diameter category was the most abundant in burned areas, which differs from what was found in this investigation, since the 20-25 cm category was the most abundant in 2013. This may be due from the fact that the authors only measured burned sites west of the BLP. In 2020, the category with the largest number of individuals was 25-30 cm, but without an increase in the previous category, which can be attributed to the lower incorporation in this category as a result of the loss of trees from the fire of 2012 that affected about 8 thousand hectares (Gallegos et al., 2014).

In SQ, in the years 2012 to 2017, sanitation actions were carried out in OF and MOPF areas due to outbreaks of Dendroctonus mexicanus Hopkins (1905) bark beetles and mistletoe (Semarnat Notifications 2012 to 2017 http://sngf.semarnat. gob.mx:8080/sngfev2/servlet/sngf) (Trigueros et al., 2014), which coincides with the decrease in BA in OF (Table 4). The remaining trees in the sites reached the following diameter category in the period as shown in Figure 2e; however, the infestation continued until 2018, causing loss of trees, which is reflected in the decrease of the 20-25 cm category in 2020. For its part, in the 2020 remeasurement, in the SDTF of the Ambrosio ejido and the OF of the Tenamaxtlán ejido, the sites were without vegetation due to the extraction of firewood for the production of charcoal.

Tree density

In BLP, the average density in 2013 was 288 trees ha^-1. This finding differs from what was reported by Gallegos et al. (2014) who counted 213 trees ha^-1. Castañeda-González et al. (2012) registered for BLP, an average of 536 trees ha^-1 and Balderas et al. (2013) 385 trees ha^-1. These differences can be attributed to the scale of the research, since Castañeda-González et al. (2012) and Gallegos et al. (2014) measured only sites affected by fires, while Balderas et al. (2013) only mixed forests unaffected by recent fires, but it can also be the result of the variation in density in BLP (Table 3).

Gallegos et al. (2014) mentioned that the return interval between high intensity fires is only 7 years in BLP, which has not allowed regeneration to be established in the damaged areas, and its effect on density is related to the intensity of the fire that causes the loss of trees (Cadena–Zamudio et al., 2022).

In Sierra de Quila, since there is no impact by fire, the disturbance factor that can be decisive in the regulation of tree density is the attack of pests, similar to what Alfaro-Reyna et al. (2022) in pine and oak forests in Tamaulipas State.

Návar-Cháidez and González-Elizondo (2009) argued that the density is modified as a result of the intraspecific competition of the species, so that in monospecific forests it tends to be lower than in mixed forests, which coincides with what was found in SQ, but it differs with what was found for BLP (Table 2).

The dispersion of density in the APFF BLP and SQ is characteristic of patchy forests (Gadow et al., 2007). The averages in the MOPF (468 trees ha^-1) and BMPE (201 trees ha^-1) in the BLP in the year 2020 (Table 2) are less than the 500 trees ha^-1 calculated by Luján (2021) for the mixed and irregular forests of the region of El Salto, Durango, but they coincide with what Baez et al. (2015) in pine-oak forests (490 trees ha^-1), where the authors associated the largest number of trees with a high diversity of species.

The attack of pests and diseases is the main disturbance factor that affects the density in SQ, as pointed out by Trigueros et al. (2014). The opposite happens in the BLP, where anthropic factors such as fire, serve as an indirect regulator of forest density.

Increase in Basimetric Area

BA in the BLP during the 15-year period increased by 3 m² ha^-1 with an IPA of 0.21 m² ha^-1 year^-1, while in SQ it was 4 m² ha^-1 in the same period with an IPA of 0.27 m² ha^-1 year^-1, which indicates that there is growth in both APFF despite the fact that there are times and types of vegetation with BA loss. Návar-Cháidez and González-Elizondo (2009) mentioned that growth tends to increase with the increase in the removal of the basimetric area in Durango forests, since competition decreases and the remaining trees increase in diameter in response (Baez et al.,2015).

The difference in IPA between APFF is not significant (p=0.505). In BLP, the IPA increases significantly (p<0.001) between periods, while in SQ it a decreases (Table 5).

In BLP, the frequency and magnitude of fires is what affects BA to a greater extent (Balderas et al., 2013). The 2005 fire according to Castañeda-González et al. (2012), caused a loss of 10 m² ha^-1, while Huerta-Martínez and Ibarra-Montoya (2014) recorded a loss of 1.31 % of forest mass in BLP due to fires that occurred from 1998 to 2012, which may be the cause of the loss of basimetric area but also that the IPA of the remaining trees increases significantly (Table 1).

In SQ, Baez et al. (2015) established that the increase in BA is modified by factors such as competition, diseases and pests (Alfaro-Reyna et al., 2022), as it happens in SQ where BA decreases between periods for OF and MOPF (Table 4).

Balderas et al. (2013) calculated 17 m² ha^-1 of BA for the MOPF in BLP for the year 2013, which coincides with the results of this research. BA in SQ (Table 3) is similar to what Dávila-Lara et al. (2019) found in mixed pine-oak forests of San Luis Potosí (18.9 m² ha^-1), but it is lower compared to the mixed forests managed in Durango (21.77 m² ha^-1) (Chávez-Flores et al., 2020).

On the other hand, the loss of BA in a forest is due to the effect of human activities such as inappropriate forest management (Návar-Cháidez and González-Elizondo, 2009), land use change, forest fires (Huerta-Martínez and Ibarra-Montoya, 2014) or the absence of management. In this study, the presence of some factors was identified that could explain the reduction in the increment BA in the sampling sites in the two APFF, such as the change in land use, grazing, the opening of spaces for walkers and fires forests, which coincide with the decrease in the increment in BA in both APFF. 

Comparison of the APFF Bosque La Primavera and Sierra de Quila

Composition in the two APFF is different in terms of the species with the greatest presence; Quercus magnolifolia is the dominant species in BLP, while Quercus resinosa is in SQ, which coincides with what was indicated by Trigueros et al. (2014) and Cadena-Zamudio et al. (2022). The diameter structure is similar in both areas because they are irregular forests similar to a J (Gadow et al., 2007), in which the most recurrent category is that of 10-15 cm dn, depending on the species.

Tree density is higher in SQ than in BLP, especially in MOPF, MPOF and SDTF. Forestry management is not applied in both areas. Therefore, they present a high variability in density, in addition to the fact that there is a loss of individuals attributable to fires and unregulated felling.

BA in both SQ and BLP, increased in all types of vegetation in the study period, with the exception of SDTF in SQ. The behavior of the IPA in BA between APFF resulted with differences in the period. It is noteworthy that the IPA in BA went from having a negative to a positive trend in the mixed forests of BLP, while the SBC of SQ is negative throughout the period.

Finally, it is important to mention that the proximity of BLP to the ZMG influences the recurrence of fires and the change in land use, phenomena that are of anthropic origin (Balderas et al., 2013), which is also observed in SQ with the extraction of individuals for firewood and charcoal. However, the variables analyzed in this study in SQ are modified as a consequence of the application of clearing cuts due to pest attacks.

Conclusions

The diametric structures of BLP and SQ indicate that trees with diameters of up to 20 cm predominate, although there are also specimens with diameters greater than 40 cm, but they are scarce. The species with the highest BA for both APFF have an inverted J-shaped diametric structure, which reflects a constant incorporation of individuals into their populations, despite the anthropic pressure to which they are subjected. BA in BLP was modified in part by the loss of individuals due to anthropic factors such as fires, land use change and lack of management. For its part, the BA in SQ varied in part due to natural factors such as mortality caused by pest attacks, although some anthropic factors such as the cutting of individuals for the production of firewood and charcoal have also influenced this change.

The AB increased in both BLP and SQ in the study period and was higher in SQ. The IPA in BA showed a negative trend in the 2005-2013 period in both APFF, which coincides with a high incidence of fires in BLP, as well as with the application of treatment to combat pests in SQ, although extraction continued of infested and dead individuals until the year 2018.

The anthropic pressure in the BLP caused by its proximity to the ZMG causes fires to frequently occur and, therefore, is one of the possible factors that determine the modification of the structure of the arboreal community analyzed. The alteration of these variables in SQ may also be due to the effect of disturbance factors such as pest attacks.

Acknowledgements

To Bosque La Primavera and Sierra de Quila Decentralized Public Bodies for allowing access to the APFF, for their support in logistics, as well as to all the staff who accompanied us on the tours. To Conahcyt for granting the Scholarship to the main author.

Conflict of interest

The authors declare they have no conflicts of interest.

Contribution by author

Consuelo Marisel Figueroa Navarro: drafting of the document, preparation of the project, data collection in the field and office work; Eduardo Salcedo Pérez: preparation of the research proposal, review of the writing and interpretation of results; Agustín Gallegos Rodríguez: data analysis and interpretation of results; Benedicto Vargas Larreta: manuscript review; Francisco Martín Huerta Martínez: review of the manuscript; Gregorio Ángeles Pérez: review of the manuscript and data analysis.

References

Aguirre C., O. A., J. Jiménez P., H. Kramer y A. Akça. 2003. Análisis estructural de ecosistemas forestales en el Cerro del Potosí, Nuevo León, México. Ciencia UANL 6(2):219-225. https://www.redalyc.org/pdf/402/40260210.pdf. (22 de septiembre de 2022).

Alfaro-Reyna, T., J. Delgado-Balbuena, X. García-Cuevas, G. Chávez-Aguilar y J. A. Estrada-García. 2022. Cambios en la estructura y composición forestal en un bosque de pino-encino en Jaumave, Tamaulipas, México. Revista e-CUCBA 9(18):40-46. Doi: 10.32870/ecucba.vi18.239.

Álvarez C., M. D. 2016. El ocio y la cultura ambiental en áreas naturales de Guadalajara: el Bosque La Primavera y la Barranca de Santiago. Tesis de Doctorado en Ciencias Sociales. Centro de Investigaciones y Estudios Superiores en Antropología Social. El Colegio de Jalisco. Guadalajara, Jal., México. 251 p.

Alvis G., J. F. 2009. Análisis estructural de un bosque natural localizado en zona rural del Municipio de Popayán. Facultad de Ciencias Agropecuarias 7(1):115-122. https://revistas.unicauca.edu.co/index.php/biotecnologia/article/view/710/338. (13 de febrero de 2022).

Báez, S., A. Malizia, J. Carilla, C. Blundo, … and K. J. Feeley. 2015. Large-scale patterns of turnover and basal area change in Andean forests. PLoS ONE 10(5):e0126594. Doi: 10.1371/journal.pone.0126594.

Balderas T., A. y J. C. Lovett. 2013. Using basal area to estimate aboveground carbon stocks in forests: La Primavera Biosphere’s Reserve, Mexico. Forestry: An International Journal of Forest Research 86(2):267-281. Doi: 10.1093/forestry/cps084.

Balderas T., A., R. Ontiveros E., M. Skutsch and J. C. Lovett. 2013. Potential for climate change mitigation in degraded forests: a study from La Primavera, Mexico. Forests 4(4):1032-1054. Doi: 10.3390/f4041032.

Bisquerra A., R. 1987. La prueba de Levene para la homogeneidad de varianzas en el BMDP. Revista de Investigación Educativa 5(9):79-85. https://digitum.um.es/digitum/bitstream/10201/96084/1/04_V5_N9_1987.pdf. (15 de abril de 2023).

Cadena-Zamudio, D. A., J. G. Flores-Garnica, M. E. Lomelí-Zavala and A. G. Flores-Rodríguez. 2022. Does the severity of a forest fire modify the composition, diversity and structure of temperate forests in Jalisco? Revista Chapingo Serie Ciencias Forestales y del Ambiente 28(1):3-20. Doi: 10.5154/r.rchscfa.2020.12.076.

Castañeda-González, J. C., A. Gallegos-Rodríguez, M. Sánchez-Durán y P. A. Domínguez-Calleros. 2012. Biomasa aérea y posibles emisiones de CO₂ después de un incendio; caso del Bosque La Primavera, Jalisco, México. Ra Ximhai 8(3):1-15. https://www.redalyc.org/articulo.oa?id=46125176001. (11 de agosto de 2022).

Chávez-Flores, G. A., J. J. Corral-Rivas, J. D. Vega-Nieva, P. M. López-Serrano y E. A. Rubio-Camacho. 2020. Estructura espacial de los bosques mixtos e irregulares en el estado de Durango. Revista Mexicana de Ciencias Forestales 11(59):141-162. Doi: 10.29298/rmcf.v11i59.614.

Comisión Nacional de Áreas Naturales Protegidas (Conanp). 2022. Ficha Técnica del Sistema de Información, Monitoreo y Evaluación Sierra de Quila. https://simec.conanp.gob.mx/ficha.php?anp=64&reg=6. (15 de abril de 2023).

Comisión Nacional Forestal (Conafor). 2019. Inventario Nacional Forestal y de Suelos. Procedimientos de muestreo. Versión 19.0. Secretaría del Medio Ambiente y Recursos Naturales (Semarnat). Zapopan, Jal., México. 311 p.

Dávila-Lara, M. A., O. A. Aguirre-Calderón, E. Jurado-Ybarra, E. Treviño-Garza, M. A. González-Tagle y G. Trincado. 2019. Estructura y diversidad de especies arbóreas en bosques templados de San Luis Potosí, México. Ecosistemas y Recursos Agropecuarios 6(18):399-409. Doi: 10.19136/era.a6n18.2112.

Flores A., A., J. J. Reynoso D., L. Hernández L. y E. A. Suárez M. 2013. Monocotiledóneas del área natural protegida Sierra de Quila, Jalisco, México. Ibugana 4:39-58. https://www.organicaeditores.mx/pdf/ibugana_4.pdf. (29 de marzo de 2021).

Flores T., C. E. y K. L. Flores C. 2021. Pruebas para comprobar la normalidad de datos en procesos productivos: Anderson-Darling, Ryan-Joiner, Shapiro-Wilk y Kolmogórov-Smirnov. Societas, Revista de Ciencias Sociales y Humanísticas 23(2):83-97. http://portal.amelica.org/ameli/jatsRepo/341/3412237018/index.html. (15 de abril de 2023).

Gadow, K. v., S. Sánchez O. y J. G. Álvarez G. 2007. Estructura y crecimiento del bosque. Universidad de Göttingen. Göttingen, NI, Alemania. 288 p. https://www.researchgate.net/publication/265270198_Estructura_y_Crecimiento_del_Bosque. (11 de septiembre de 2022).

Gallegos R., A., G. A. González C., R. G. Cabrera O., C. Marcelli S. y E. Hernández Á. 2014. Efecto de la recurrencia de incendios forestales en la diversidad arbórea. Revista Mexicana de Ciencias Forestales 5(24):110-125. Doi: 10.29298/rmcf.v5i24.324.

García, E. 2004. Modificaciones al sistema de clasificación climática de Köppen. Serie Libros, Núm. 6. Instituto de Geografía, Universidad Nacional Autónoma de México. Coyoacán, D. F., México. 90 p.

González O., H. A., P. Cortés-Calva, L. I. Íñiguez D. y A. Ortega-Rubio. 2014. Las áreas naturales protegidas de México. Investigación y Ciencia 22(60):7-15. https://www.redalyc.org/articulo.oa?id=67431160002. (26 de marzo de 2022).

González-Abraham, C., E. Ezcurra, P. P. Garcillán, A. Ortega-Rubio, M. Kolb and J. E. Bezaury C. 2015. The human footprint in Mexico: physical geography and historical legacies. PLoS ONE 10(3):e0121203. Doi: 10.1371/journal.pone.0121203.

Huerta-Martínez, F. M. y J. L. Ibarra-Montoya. 2014. Incendios en el Bosque La Primavera (Jalisco, México): un acercamiento a sus posibles causas y consecuencias. CienciaUAT 9(1):23-32. Doi: 10.29059/cienciauat.v9i1.304.

Luján S., J. E. 2021. Nuevas alternativas silvícolas para el aprovechamiento sustentable de los bosques mixtos e irregulares en Durango, México. Tesis de Doctorado en Ciencias con orientación en Manejo de Recursos Naturales. Facultad de Ciencias Forestales, Universidad Autónoma de Nuevo León. Linares, N. L., México. 55 p.

Maldonado I., O. A., R. M. Chávez D. y M. L. Bravo O. 2020. Áreas naturales protegidas y participación social en América Latina: problemas y estrategias para lograr la integración comunitaria. Región y Sociedad 32:e1277. Doi: 10.22198/rys2020/32/1277.

Návar-Cháidez, J. J. y S. González-Elizondo. 2009. Diversidad, estructura y productividad de bosques templados de Durango, México. Polibotánica 27:71-87. http://www.scielo.org.mx/scielo.php?script=sci_arttext&pid=S1405-27682009000100005&lng=es&nrm=iso. (30 de enero de 2022).

R Core Team. 2020. R: A language and environment for statistical computing (version 4.1.1). Vienna, W, Austria. R Foundation for Statistical Computing. https://www.R-project.org/. (15 de abril de 2023).

Rzedowski, J. 2006. Vegetación de México. Comisión Nacional para el Conocimiento y Uso de la Biodiversidad. Tlalpan, Cd. Mx., México. 504 p.

Secretaría del Medio Ambiente y Recursos Naturales (Semarnat). 2001. Resumen del programa de manejo del Área Natural Protegida con el carácter de Área de Protección de Flora y Fauna La Primavera. Diario Oficial de la Federación, 22 de mayo de 2001. https://dof.gob.mx/nota_detalle.php?codigo=766100&fecha=22/05/2001#gsc.tab=0. (22 de febrero de 2020).

Systat Software Inc. 2012. Sigma Plot para Windows versión 12.0. Build 12.0.0.182. Palo Alto, CA, United States of America. Systat https://systatsoftware.com/sigmaplot/. (15 de abril de 2023).

Trigueros B., A. G., R. Villavicencio G. y A. L. Santiago P. 2014. Mortalidad y reclutamiento de árboles en un bosque templado de pino-encino en Jalisco. Revista Mexicana de Ciencias Forestales 5(24):160-183. Doi: 10.29298/rmcf.v5i24.327.

Villavicencio G., R., A. L. Santiago P., J. J. Godínez H., J. M. Chávez A. y S. L. Toledo G. 2012. Efecto de la fragmentación sobre la regeneración natural de la Sierra de Quila, Jalisco. Revista Mexicana de Ciencias Forestales 3(11):9-23. Doi: 10.29298/rmcf.v3i11.514.

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