# Postfire Burnt-Wood Management Affects Plant Damage by Ungulate Herbivores

Authors: Jorge Castro
Journal: International Journal of Forestry Research
 (2013)

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## Abstract

I analyze the effect of post-fire burnt wood management on herbivore attack on a woody plant species (Ulex parviflorus). Two experimental plots of ca. 20 hectares were established at two elevations in a burnt area in a Mediterranean mountain (Sierra Nevada, Spain). Three replicates of three treatments differing in post-fire burnt wood management were established per plot: “no intervention” (NI, all trees remained standing), “partial cut plus lopping” (PCL, felling the trees, cutting the main branches, and leaving all the biomass in situ), and “salvage logging” (SL; removal of logs and elimination of woody debris). Risk of herbivory and damage intensity were monitored for two years. The pattern of attack by ungulate herbivores varied among treatments and years. In any case, there was an overall reduction in the risk of herbivory in the PCL treatment, presumably because the highest habitat complexity in this treatment hampered ungulate movement and foraging. As a result, the burnt logs and branches spread over the ground acted as a physical barrier that protected seedlings from herbivores. This protection may be used for the regeneration of shrubs and trees, and it is of interest for the regeneration of burnt sites either naturally or by reforestation.


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## Body

## 1. Introduction

A current controversial issue among restoration ecologists and forest managers concerns the appropriate management of dead burnt trees after fire. Post-fire salvage logging (i.e., the felling and removal of the burnt tree trunks, often eliminating the remaining woody debris by chipping, mastication, fire, etc.) has historically been routinely and widely practiced by forest administrations around the world [1–4], particularly in the case of burnt conifer forests. However, there is currently an intense debate about the suitability of this approach [5–8]. A growing number of studies show that salvage logging may increase soil erosion, diminish the regeneration capacity due to seedling bank or resprout destruction, or reduce the biodiversity of plants and animals [1, 3, 6, 8], among other processes. As a result, there are increasing calls for less aggressive post-fire intervention policies, associated with evidence that snags and decaying burnt wood are components of natural systems that promote ecosystem recovery and diversity [4, 5, 9–12].An important topic to be considered for the post-fire regeneration of woody vegetation is the effect of ungulate herbivores. Movement and foraging behavior of ungulates is conditioned by habitat characteristics at different spatial scales [13–16]. These characteristics may be related to food-selection preferences according to the palatability of the patch, the accessibility to the area, or to the predation risk suffered by ungulates, among other factors [14, 17–21]. Ungulates are, on the other hand, one of the main factors hampering the success of reforestation efforts as well as natural post-fire recovery of the vegetation [22–25]. Thus, it is likely that the post-fire management of the burnt wood will alter the use of the habitat by ungulate herbivores, as it has the potential to alter accessibility or protection against predators, among other factors (e.g., [20, 27, 28]). The degree that salvage logging changes the habitat could be then of great importance for ungulate foraging decisions and thus determine their impact in the recovering, post-fire plant community. However, little information is available on the effect of salvage logging versus other post-fire management alternatives on the damage of vegetation by ungulate herbivores.In the present study, I analyze the effect that burnt-wood management exerts on the herbivory undergone by a woody plant species recovering in a burnt area. The burnt wood was experimentally managed to create three scenarios that differed in habitat structure. For the target species, I used a legume shrub (Ulex parviflorus Pourr.; Fabaceae), an obligate seeder that regenerates quickly and abundantly after fires in the Mediterranean region [29, 30]. Ulex species also constitute an important component of the diet of domestic livestock and wild ungulates [31, 32], being therefore an appropriate model to test the effect that habitat structure via burnt-wood management exerts on the risk and magnitude of herbivory soon after the fire. I hypothesise that post-fire burnt-wood management will influence the rate of herbivore damage, as the experimental treatments used contrast sharply in habitat characteristics, ranging from a landscape without tree overstory in salvaged areas to a habitat that still has an overstory of branches and logs in the other treatments.


## 2. Methods

### 2.1. Study Site, Target Species, and Experimental Design

The study site was located in Sierra Nevada National and Natural Park (SE Spain), where in September 2005 the Lanjarón fire burned ca. 1,300 hectares of pine reforestations with trees of 35 to 45 years old, depending on the stand. Two plots were established after the fire at different altitudinal levels. The plots were homogeneous in terms of orientation (SW), slope (ca. 30%), fire intensity (high intensity), bedrock (mica schist), and pretreatment tree characteristics. Plot 1 (17.7 hectares in size) was located at 1477 m a.s.l. (ED 50/UTM zone 30N, positionx, y: 456070, 4089811) and plot 2 (of 23.9 hectares) at 1698 m (position x, y: 455449, 4091728; altitude and position measured at the centroid of the plot). The pine species present in each plot differed according to their ecological requirements along this elevational gradient. The cluster pine (Pinus pinaster) and the black pine (P. nigra) dominated in plot 1, whereas the black pine dominated in plot 2. Both pine species are native in the region, although they were extensively planted in the area for forestry purposes. The climate of the area is Mediterranean type, with rainfall concentrated in spring and autumn, alternating with hot, dry summers. Mean annual precipitation at the lowest plot was 466 mm (1988–2008 period; climatic data from a meteorological station beside plot 1). The mean annual temperature was 11.9°C at 1652 m a.s.l. (State Meteorological Agency, period 1994–2008; Ministry of Environment).Within each plot, three replicates of the following treatments were implemented in a random spatial distribution: (1) “nonintervention” (NI), leaving all of the burnt trees standing; (2) “partial cut plus lopping” (PCL), a treatment where ca. 90% of burned trees were cut and felled, with the main branches also lopped off, but leaving all the cut biomassin situ on the ground; after treatment application, felled logs and branches covered 45% of the surface at 0–10 cm from the ground, 61% at 11–50 cm, and 9% at 51–100 cm [12]; (3) “salvage logging” (SL), where tress were cut and the trunks cleaned of branches with the use of chainsaws. Trunks were manually piled (groups of 10–15) and the woody debris was masticated using a tractor. The Forest Service planned to remove the trunks with a log forwarder in this treatment, but this step was later cancelled due to difficulties in precisely operating machinery within the spatial arrangement of the plots.The resulting 18 experimental replicates had a size that ranged from 1.2 to 3.5 hectares (average of2.34±0.14; mean ± SE), with no differences among treatments (Kruskal-Wallis test, P>0.05). Salvage logging is the usual post-fire action taken by the local Forest Service, and it was fully implemented throughout the rest of the burnt area where the experimental plots were located. The three treatments differed therefore in the degree of intervention (maximum in SL, intermediate in PCL, and minimum in NI) and in the habitat structure generated (minimum habitat complexity in SL and maximum in PCL; [12, 33]). All post-fire management treatments were implemented during March to May 2006 (ca. seven months after the 2005 forest fire). The fire was moderate to high in severity, consuming or totally scorching most of the tree crown. Tree density before treatment implementation was 1477±46 individuals per hectare for plot 1 and 1064±67 for plot 2. Basal tree diameter was 17.7±0.2 cm in plot 1 and 18.3±0.1 in plot 2 [34].Ulex parviflorus is one of the most common seeder species that colonize postburnt areas in the western Mediterranean basin [29, 30]. Like other gorse species (e.g., [32]), U. parviflorus is consumed by domestic and wild ungulates in the Mediterranean basin [31]. The species was one of the few woody plants that appeared abundantly in the area after the fire and was present in almost all the replicates of the experiment (see below).


### 2.2. Seedling Monitoring

In June 2006, I randomly chose and marked 50 seedlings ofU. parviflorus per replicate and treatment at each of the two plots. One of the replicates of treatment PCL in plot 2 had no seedlings and could not be included in the study. This resulted in 3 treatments × 3 replicates × 50 seedlings (450 seedlings) for plot 1 and 400 seedlings for plot 2. Seedling survival, growth, and damage by ungulate herbivores were monitored in October 2006 (thus after the first growing season) and October 2007 (second growing season). Growth parameters included plant height and crown diameter (two perpendicular diameters). Damage by ungulate herbivores (mostly the wild goat Ibex hispanica in the area, and to a lesser extent domestic goats and sheep) was sampled by counting the number of damaged and intact shoots for the first and second growing season. To analyse the herbivore damage, I estimated two indices: (i) risk of herbivory, percentage of U. parviflorus plants that underwent at least one event of ungulate damage, and (ii) damage intensity (only for seedlings undergoing herbivory), proportion of the shoots consumed by ungulates. The initial height of the seedlings was 14.6±0.3 cm for plot 1 and 13.4±0.3 cm for plot 2, and ranged between 13.2±0.4 cm in NI and 15.2±0.4 cm in SL (plots pooled).The vegetation cover may affect herbivore selection at the patch level [14, 18]. Thus, I sampled vegetation cover in June 2006, expressed as the number of individuals per square meter. For this, I randomly established 8 transects of 50 × 2 m size per replicate (placed with their longest dimension along the maximum slope of the terrain) and counted the number of individuals of all the species.


### 2.3. Data Analyses

Given that one of the replicates of treatment PCL in plot 2 lackedUlex parviflorus seedlings, I performed the analyses pooling the data of the 2-3 replicates of each treatment per plot. Seedling growth was analysed with mixed two-way ANOVAs, with Plot as a random factor and Treatment as a fixed factor. Trends were similar across years, and only data of the last growing season (after two years) were reported for simplicity. For plant diameter, there was a strong correlation between the two perpendicularly measured diameters (r2=0.68; P<0.0001), and the mean of the two diameters per plant was used as the dependent variable (canopy diameter, hereafter). Risk of herbivory was analysed with a nominal logistic model, considering simultaneously the effect of Plot and Treatment. Damage intensity was analysed with a two-way ANOVA (data arc-sin transformed), considering similarly Plot as a random factor and Treatment as a fixed factor. The relationship between vegetation cover and herbivore attack (risk of herbivory) was explored for year 2006 with a regression analysis using mean cover per replicate as the independent variable. Statistical analyses were performed with JMP 7.0 software (SAS Institute). Throughout the paper, values are mean ± 1SE.


## 2.1. Study Site, Target Species, and Experimental Design

The study site was located in Sierra Nevada National and Natural Park (SE Spain), where in September 2005 the Lanjarón fire burned ca. 1,300 hectares of pine reforestations with trees of 35 to 45 years old, depending on the stand. Two plots were established after the fire at different altitudinal levels. The plots were homogeneous in terms of orientation (SW), slope (ca. 30%), fire intensity (high intensity), bedrock (mica schist), and pretreatment tree characteristics. Plot 1 (17.7 hectares in size) was located at 1477 m a.s.l. (ED 50/UTM zone 30N, positionx, y: 456070, 4089811) and plot 2 (of 23.9 hectares) at 1698 m (position x, y: 455449, 4091728; altitude and position measured at the centroid of the plot). The pine species present in each plot differed according to their ecological requirements along this elevational gradient. The cluster pine (Pinus pinaster) and the black pine (P. nigra) dominated in plot 1, whereas the black pine dominated in plot 2. Both pine species are native in the region, although they were extensively planted in the area for forestry purposes. The climate of the area is Mediterranean type, with rainfall concentrated in spring and autumn, alternating with hot, dry summers. Mean annual precipitation at the lowest plot was 466 mm (1988–2008 period; climatic data from a meteorological station beside plot 1). The mean annual temperature was 11.9°C at 1652 m a.s.l. (State Meteorological Agency, period 1994–2008; Ministry of Environment).Within each plot, three replicates of the following treatments were implemented in a random spatial distribution: (1) “nonintervention” (NI), leaving all of the burnt trees standing; (2) “partial cut plus lopping” (PCL), a treatment where ca. 90% of burned trees were cut and felled, with the main branches also lopped off, but leaving all the cut biomassin situ on the ground; after treatment application, felled logs and branches covered 45% of the surface at 0–10 cm from the ground, 61% at 11–50 cm, and 9% at 51–100 cm [12]; (3) “salvage logging” (SL), where tress were cut and the trunks cleaned of branches with the use of chainsaws. Trunks were manually piled (groups of 10–15) and the woody debris was masticated using a tractor. The Forest Service planned to remove the trunks with a log forwarder in this treatment, but this step was later cancelled due to difficulties in precisely operating machinery within the spatial arrangement of the plots.The resulting 18 experimental replicates had a size that ranged from 1.2 to 3.5 hectares (average of2.34±0.14; mean ± SE), with no differences among treatments (Kruskal-Wallis test, P>0.05). Salvage logging is the usual post-fire action taken by the local Forest Service, and it was fully implemented throughout the rest of the burnt area where the experimental plots were located. The three treatments differed therefore in the degree of intervention (maximum in SL, intermediate in PCL, and minimum in NI) and in the habitat structure generated (minimum habitat complexity in SL and maximum in PCL; [12, 33]). All post-fire management treatments were implemented during March to May 2006 (ca. seven months after the 2005 forest fire). The fire was moderate to high in severity, consuming or totally scorching most of the tree crown. Tree density before treatment implementation was 1477±46 individuals per hectare for plot 1 and 1064±67 for plot 2. Basal tree diameter was 17.7±0.2 cm in plot 1 and 18.3±0.1 in plot 2 [34].Ulex parviflorus is one of the most common seeder species that colonize postburnt areas in the western Mediterranean basin [29, 30]. Like other gorse species (e.g., [32]), U. parviflorus is consumed by domestic and wild ungulates in the Mediterranean basin [31]. The species was one of the few woody plants that appeared abundantly in the area after the fire and was present in almost all the replicates of the experiment (see below).


## 2.2. Seedling Monitoring

In June 2006, I randomly chose and marked 50 seedlings ofU. parviflorus per replicate and treatment at each of the two plots. One of the replicates of treatment PCL in plot 2 had no seedlings and could not be included in the study. This resulted in 3 treatments × 3 replicates × 50 seedlings (450 seedlings) for plot 1 and 400 seedlings for plot 2. Seedling survival, growth, and damage by ungulate herbivores were monitored in October 2006 (thus after the first growing season) and October 2007 (second growing season). Growth parameters included plant height and crown diameter (two perpendicular diameters). Damage by ungulate herbivores (mostly the wild goat Ibex hispanica in the area, and to a lesser extent domestic goats and sheep) was sampled by counting the number of damaged and intact shoots for the first and second growing season. To analyse the herbivore damage, I estimated two indices: (i) risk of herbivory, percentage of U. parviflorus plants that underwent at least one event of ungulate damage, and (ii) damage intensity (only for seedlings undergoing herbivory), proportion of the shoots consumed by ungulates. The initial height of the seedlings was 14.6±0.3 cm for plot 1 and 13.4±0.3 cm for plot 2, and ranged between 13.2±0.4 cm in NI and 15.2±0.4 cm in SL (plots pooled).The vegetation cover may affect herbivore selection at the patch level [14, 18]. Thus, I sampled vegetation cover in June 2006, expressed as the number of individuals per square meter. For this, I randomly established 8 transects of 50 × 2 m size per replicate (placed with their longest dimension along the maximum slope of the terrain) and counted the number of individuals of all the species.


## 2.3. Data Analyses

Given that one of the replicates of treatment PCL in plot 2 lackedUlex parviflorus seedlings, I performed the analyses pooling the data of the 2-3 replicates of each treatment per plot. Seedling growth was analysed with mixed two-way ANOVAs, with Plot as a random factor and Treatment as a fixed factor. Trends were similar across years, and only data of the last growing season (after two years) were reported for simplicity. For plant diameter, there was a strong correlation between the two perpendicularly measured diameters (r2=0.68; P<0.0001), and the mean of the two diameters per plant was used as the dependent variable (canopy diameter, hereafter). Risk of herbivory was analysed with a nominal logistic model, considering simultaneously the effect of Plot and Treatment. Damage intensity was analysed with a two-way ANOVA (data arc-sin transformed), considering similarly Plot as a random factor and Treatment as a fixed factor. The relationship between vegetation cover and herbivore attack (risk of herbivory) was explored for year 2006 with a regression analysis using mean cover per replicate as the independent variable. Statistical analyses were performed with JMP 7.0 software (SAS Institute). Throughout the paper, values are mean ± 1SE.


## 3. Results and Discussion

Survival after two years was high in all the experimental replicates, with overall values of 88.9% in NI, 94.5% in PCL, and 95.7% in SL (the two plots pooled), supporting thatUlex parviflorushas a high regeneration capacity after fire (e.g., [30]). Among the surviving seedlings, canopy diameter was affected by Plot and Treatment (Table 1). Plants had a higher canopy diameter at the lowest elevation, with values of 40.1±1.2 cm for NI, 41.1±1.3 cm in PCL, and 42.6±1.2 cm in SL for plot 1 and 37.5±1.2, 28.6±1.9, and 32.8±0.9, respectively, for plot 2 (resulting therefore in a significant Plot × Treatment interaction; Table 1). Plants had similarly higher height at the lowest elevation (Table 1), with values of 43.2±1.6 cm for NI, 47.9±1.4 cm in PCL, and 44.0±1.4 cm in SL for plot 1 and 37.3±1.4, 38.1±1.4, and 35.5±1.1, respectively, for plot 2. This was likely due to the altitudinal level, since in plot 2, at around 1700 m a.s.l., U. parviflorus is at its altitudinal upper limit in the area, whereas at 1400 m it finds appropriate conditions for growth [35]. In any case, differences among treatments were low within plot, and thus it is unlikely that ungulate selection of habitat for foraging could be mediated by plant size. Furthermore, there was no relationship between mean values of plant size per replicate and mean values of damage by herbivores (data not shown).Table 1
Summary of the two-way ANOVAs for growth parameters measured inUlex parviflorus plants after two growing seasons (October 2007). Treatments are no intervention, partial cut plus lopping, and salvage logging.
Variable
Factor
d.f.
F-ratio
P
Canopy diameter
Plot (P)
1
71.31
<0.0001
Treatment (T)
2
5.40
0.0047
P
×
T
2
8.86
0.0002
Error
721
Plant height
Plot (P)
1
48.78
<0.0001
Treatment (T)
2
2.91
0.0552
P
×
T
2
1.02
0.3606
Error
722Vegetation cover (estimated as density of individuals) differed among treatments in the two plots (F≥3.68, d.f. = 2, 69, P≤0.0302). In plot 1, the highest value was recorded in NI (3.45±0.38 seedlings m−2), followed by PCL (3.12±0.31) and SL (2.43±0.28). In plot 2, the highest was recorded in PCL (5.70±0.76), followed by NI (4.50±0.37) and SL (3.19±0.33; seedlings m−2 in all cases). Nonetheless, the risk of herbivory was not related to the cover of vegetation (F=0.49, d.f. = 1, 15, P=0.4932).Risk of herbivory differed significantly among plots and treatments for the two years (Table2). The pattern among treatments changed among plots and years (significant interactions), but PCL was in general the treatment with the lowest values of plants attacked (except plot 1 in year 2006, when NI had lower values; Table 3), with an overall value of 28.5% for PCL treatment, 38.8% for NI, and 40.8% for SL (all plots and years pooled). The level of damage undergone by a target plant may be inversely related to the difficulty or the risk that the herbivore faced in finding the food in a heterogeneous landscape [14, 18, 20]. In this sense, the highest habitat complexity generated by felled logs and branches spread on the ground could hamper the movement of large herbivores in the area, as reported previously in the study site for another ungulate, the wild boar (e.g., [33]). Damage intensity was similar among plots and treatments (Table 2). There were, however, marginally significant differences among treatments in the first year, with the highest value in PCL (42.9±3.8%), followed by SL (34.8±2.4) and NI (31.2±2.3; the two plots pooled). This result still supports the hypothesis of a reduced ungulate presence in the PCL treatment despite this one having the highest value of damage for the first year: in a situation of more difficulty to find the plants, herbivores likely made more use of the Ulex found in order to compensate for the time invested in foraging [18]. Thus, in short, the results show that post-fire burnt-wood management altered the habitat choice of ungulates and support that burnt logs and branches spread on the ground provided a physical barrier that protected the seedlings against ungulate herbivores.Table 2
Summary of the nominal logistic model for risk of herbivory (proportion of plants that suffered herbivory by ungulates) and two-way ANOVA for damage intensity (proportion of shoots consumed by ungulates in attacked plants) suffered byUlex parviflorus seedlings in the years 2006 and 2007 (one- and two-year-old plants, resp.). Treatments are no intervention, partial cut plus lopping, and salvage logging.
Source
Risk of herbivory
Damage intensity
d.f.
Waldχ2
P
d.f.
F
P
Year 2006
Plot (P)
1
7.39
0.0065
1
1.42
0.3380
Treatment (T)
2
9.90
<0.0071
2
11.33
0.0811
P
×
T
2
6.86
0.0323
2
0.36
0.7008
Model/Error
5
28.10
<0.0001
212
Year 2007
Plot (P)
1
5.86
0.0155
1
1.55
0.3383
Treatment (T)
2
7.67
0.0216
2
0.75
0.5710
P
×
T
2
5.50
0.0640
2
6.88
0.0012
Model/Error
5
21.12
0.0012
264Table 3
Mean values for risk of herbivory (proportion of plants that suffered herbivory by ungulates) for years 2006 and 2007 for plants ofUlex parviflorus sampled in the experiment (one- and two-year-old plants, resp.).
NI
PCL
SL
Year 2006
Plot 1
15.9
22.8
25.0
Plot 2
31.6
19.3
41.2
Year 2007
Plot 1
38.8
21.7
41.4
Plot 2
46.4
38.2
39.2
NI: no intervention; PCL: partial cut plus lopping; SL: salvage logging.The Mediterranean gorseU. parviflorus is not a species that requires restoration efforts for its regeneration. Its ability to germinate after heat shock, its resistance to drought, fast growth rate, and early reproduction, virtually guarantee its regeneration after disturbance by fires [26, 30]. However, the results of this study support the contention that the protection offered by felled logs and branches spread over the ground could benefit either the natural regeneration or reforestation with tree species of interest for forest recovery. Ungulate herbivores are one of the main factors hampering the success of reforestations [22, 36] as well as natural post-fire recovery of the vegetation [23, 25]. It is well known that the physical barrier provided by thorny or spiny shrubs protects the seedlings and saplings of tree species in Mediterranean ecosystems as well as in other ecosystem types (e.g., [17, 18, 37–40]). This mechanism of associational resistance (sensu [18]) can also be provided by dead woody structures, which similarly hinder the ungulate access to the saplings protected under their cover. In this sense, Ripple and Larsen [41] reported the protection of aspen by coarse woody debris. Puerta-Piñero et al. [28] and Leverkus et al. [33] reported that felled burnt logs and branches reduced the impact of wild boar predation on sowed acorns, and Relva et al. [20] have shown that logs and branches that collapsed after massive die-back also reduced herbivory by deer. Moreover, the foraging behaviour of ungulate herbivores depends on the context of the target and the protector plant: the lower the palatability of the protector, the higher the chance of protection for a particular target species [17, 18]. Burnt branches offer low palatability. Thus, it is very likely that their protective role could be expanded to other species more palatable than U. parviflorus and to other systems provided that logs, branches, or both are left in situeither naturally or after management.



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*Source: 965461-2013-09-05.xml*