Nativa, Sinop, v. 11, n. 2, p. 148-160, 2023.

Pesquisas Agrárias e Ambientais

DOI: https://doi.org/10.31413/nativa.v11i2.15355

ISSN: 2318-7670

Litterfall and herbaceous plants regeneration in planted forests at post

prescribed fire in the Cerrado-Amazon transition

Ana Paula Slovinski de Oliveira CAMARGO1, Daiane Cristina de LIMA1,

Josiane Fernandes KEFFER1, Rafael ARRUDA1, Adilson Pacheco de SOUZA1*

1 Posgraduate Program in Environmental Sciences, Federal University of Mato Grosso, Sinop, MT, Brazil.

*E-mail: adilson.souza@ufmt.br

Submission: 04/20/2023; Accepted on 05/22/2023; Published on 06/12/2023.

ABSTRACT: Information on the effects of prescribed burning in forest areas is essential for numerous

environmental and forest production applications, including preventive maintenance against forest fires. In this

article, we evaluated the effects generated at different interfaces (borders) of a homogeneous area of eucalyptus,

after the occurrence of prescribed burns. The litter recovery and the regeneration of herbaceous material were

evaluated, which may compose the combustible material for the occurrence of new fires. The forest inventory

include measurements of circumference at breast height (CBH), commercial and total height, canopy density

percentage, and number alive and dead trees. The percentage of herbaceous plants and litterfall differentiation

were determined through photos taken in the field and subjected to pixel analysis in the Adobe Photoshop Cs6

program. The litterfall was classified into leaves, barks, and branches, and the herbaceous plants was subjected

to identification and quantification of phytosociological variables. The prescribed fire did not affect the survival

and development of trees, since the values were consistent with the community age. Leaves represented the

highest litterfall fraction (47.69%) and thick branches the lowest (1.79%), both in the eucalyptus/agriculture

interface. The herbaceous plants totalized 120 individuals, with predominance of grass species and had higher

abundance in the eucalyptus/agriculture and eucalyptus/forest interfaces.

Keywords: planted forests; prescribed fire; post-fire; combustible matter; regeneration; forestry.

Serrapilheira e regeneração herbácea em floresta plantada pós queimas prescritas

na transição Cerrado-Amazônia

RESUMO: Informações sobre os efeitos da queima prescrita em áreas florestais são essenciais para inúmeras

aplicações ambientais e para a produção florestal, incluindo a manutenção preventiva contra incêndios

florestais. Neste artigo, avaliamos os efeitos gerados em diferentes interfaces (bordas) de uma área homogênea

de eucalipto, após a ocorrência de queimadas prescritas. Foi avaliada a recomposição da serapilheira e a

regeneração do material herbáceo, que serão os componentes do material combustível para a ocorrência de

novos incêndios. O inventário da floresta plantada incluiu medidas de circunferência à altura do peito (CBH),

altura comercial e total, percentual de densidade de copa e número de árvores vivas e mortas. A porcentagem

de plantas herbáceas e a diferenciação da serapilheira foram determinadas por meio de fotos tiradas no campo

e submetidas à análise de pixels no programa Adobe Photoshop Cs6. A serapilheira foi classificada em folhas,

cascas e galhos, e as plantas herbáceas foram submetidas à identificação e quantificação de variáveis

fitossociológicas. O fogo prescrito não afetou a sobrevivência e o desenvolvimento das árvores, pois os valores

foram condizentes com a idade da comunidade. As folhas representaram a maior fração de serapilheira

(47,69%) e galhos grossos a menor (1,79%), ambas na interface eucalipto/agricultura. As plantas herbáceas

totalizaram 120 indivíduos, com predominância de espécies gramíneas e tiveram maior abundância nas

interfaces eucalipto/lavoura e eucalipto/floresta.

Palavras-chave: florestas plantadas; fogo prescrito; pós-fogo; matéria combustível; regeneração; silvicultura.

1. INTRODUCTION

The forest sector in Brazil has a large representativeness

in the international market of forest products, occupying the

first and second place in cellulose exports and production,

respectively, after only the United States (IBGE, 2021). Brazil

has approximately 9.93 million hectares (ha) of planted

forests ((trees planted, harvested and replanted in previously

degraded areas), with 7.53 million hectares of eucalyptus

plantations (IBÁ, 2022), with increasing expansion in all

states of Brazil.

In the state of Mato Grosso, the planted area with

eucalyptus in 2021 was 188.605 ha, with a mean increase of

28% from 2009, and an estimation of 700,000 hectares for

2028 (IBÁ, 2022). Currently, the hybrid Eucalyptus urograndis

(Eucalyptus urophylla × Eucalyptus grandis H-13) have been

planted in Mato Grosso for energy purposes focused on

meeting the wood demand due to the implementation of

several maize ethanol production industries in the region, and

demands for drying of agricultural products and

slaughterhouses (ZIERO et al., 2021).

Camargo et al.

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149

However, homogeneous forests present high risk of fire

due to the continuous accumulation leaves and branches in

the ground from plants and ground vegetation that have low

decomposition rates, which serve as combustible matter for

fires (BORGES et al., 2012). This is worrisome, mainly in

Mato Grosso, since the state presents a dry period that favors

even more the incidence of fires (CASAVECCHIA et al.,

2019).

The litterfall deposition and accumulation dynamics is

highly variable, since the quantity of matter is affected by

climate dynamics and other factors, such as the ecosystem

category, plant age, planting spacing, and plant-environment

interaction (CIZUNGU et al., 2014; ALONSO et al., 2015).

The quantification of litterfall assists in the forest protection

management for fast-growth species, such as eucalyptus,

since the biomass management can be preventively done

depending on the class of combustible matter, using efficient

prevention techniques and control of fires (BORGES et al.,

2012; ALVES et al., 2017).

Several alternatives can be adopted to mitigate or prevent

the occurrence of forest fires, which are chosen depending

on many factors, such as financial and technological

resources and state policies (BATISTA, 2009; RAMALHO

et al., 2021). The partial or total removal of combustible

matter through prescribed fire is among these options; it

presents positive results in biomass control and mitigation of

negative effects of fires (MCCAW, 2013; ALVES et al.,

2017).

Prescribed or controlled fire has been widely used as a

management tool in production systems with planted forests,

maintaining the habitat quality and stimulating regeneration

in the managed areas (BOWMAN et al., 2009;

VOGELMANN et al., 2015). According some studies, this is

a practical and efficient method for decreasing combustible

matter and prevent fires in eucalyptus forests that do not

affect tree development and assists in decreasing weed

competition, insects, fungi, and litterfall, when rationally

applied (BERENHAUSER, 1972; MCCAW, 2013;

GUIMARÃES et al., 2014; LIMA et al., 2020a).

Controlled fire in Brazil was legalized by Brazilina Forest

Code (law 12.651/2012) and the Federal Decree no. 2.661,

of 8 of July 1998, whose Article 2 considers the use of fire

for the production and management in agroforestry or forest

activities, and for scientific and technological researches in

areas with previously defined limits (BRASIL, 1998).

However, the inconsequent use of fire can reach catastrophic

proportions, by decreasing biodiversity, releasing high levels

of greenhouse gases, hindering local and regional air quality,

facilitating the entry and proliferation of invasive species, and

modifying the structure and standards of production

processes (SHLISKY et al., 2007; GUIMARÃES et al., 2014).

Therefore, information on the dynamics of Eucalyptus sp.

regarding the production of combustible matter (litterfall and

herbaceous plants) in the sub-forest, and on fire

characteristics and periods more prone for prescribed fire is

important (ALVES et al., 2017; LIMA et al., 2020a,b). Thus,

the objective of this work was to survey, evaluate, and

estimate the availability of combustible matter formed by the

litterfall and regeneration of herbaceous plants in the sub-

forest of a planted forest of eucalyptus in the Cerrado-

Amazon transition region of the state of Mato Grosso, Brazil,

in different environmental interfaces and post-controlled fire

periods.

2. MATERIALS AND METHODS

2.1. Area of study

The study was developed in the Santo Antônio Farm,

which belongs to the BRF Company (Brazil Food SA), in the

municipality of Sorriso, Mato Grosso, Brazil (12°51'44''S,

55°52'34''W, and altitude of 365 m). The predominant

climate in Sorriso is AW, hot and wet, according to the

Köppen classification, with two well-defined seasons: rainy

(October to April) and dry (May to September) (SOUZA et

al., 2013).

The experimental area was covered with forest

plantations of the species E. urograndis (hybrid clone of E.

urophylla and E. grandis - H13) with 6.5 years of age in April

2018, with spacing of 3 × 3 meters. The plantations were in

different environmental interfaces, with a border interface

with agriculture (soybean/maize/cotton) at West and an

interface with native riparian forest with plant formations

typical of arborized savannas and submountain semi-decidual

seasonal forest at East (Delmon et al., 2013), termed in this

study as eucalyptus/agriculture (EA), eucalyptus/eucalyptus

(EE) and eucalyptus/ remnant of native forest (EF)

interfaces (Figure 1). The eucalyptus plantation area in the EF

interface were partially flooded due to proximity of a lake and

the rainfall regime between October to April.

Figure 1. Experimental area with Eucalyptus urograndis plantation and delimitation of sampled plots in Sorriso, MT, Brazil.

Figura 1. Área experimental de Eucalyptus urograndis e delimitação das parcelas amostrais em Sorriso, MT, Brasil.

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150

Three prescribed fires were carried out in May 2015,

September 2015, and August 2016 in the EA, EE, and EF

interfaces of the experimental area (distant 30.0 m from the

borders), thus, they were evaluated at 36, 32, and 21 months

after the controlled fire, respectively, since the collections of

litterfall and herbaceous plants took place in April 2018. The

plots with prescribed fire were 3.0 m wide and 20.0 m long;

they were designed following the planting line and were at

the same level, with 1.0-m firebreaks in all interfaces. Three

replications were used for each interface and post-fire

periods. The control plots (reference areas) were considered

in the same environmental interfaces, however they did not

receive controlled burning and the plants were 77 months

old.

2.2. Plantation inventory

The plantation homogeneity was evaluated in the

different interfaces considering the following variables of

trees in the plots: circumference at breast height (CBH), using

a diametric tape; comercial (CH) and total height (TH), using

a clinometer; canopy density percentage, using a leveled

convex spherical densiometer in the combustible matter

collection points; and number alive and dead trees.

2.3. Combustible matter collection

Combustible matter, litterfall, and herbaceous plants in

the ground surface were collected in April 2018, in the three

environmental interfaces (Figure 2), following the

recommendations of Alves et al. (2017). Sampling points at

5, 10, and 15 m were selected in each plot; they were marked

and identified after the fire. A polyvinyl chloride frame with

area of 1.0 m² (Figure 2) was used to delimitate the sampling

points, and thin and thick branches were sectioned in the

limits of the sampling frame; then, all litterfall was collected

and stored in black plastic bags, labeled, and sent for

screening. The classification followed the methodology used

by Rothermel (1972) and Alves et al. (2017), considering the

following classes: leaves, barks, and branches. Branches were

classified according to their diameters (cm) as thin (≤0.7),

medium (≥0.7 and ≤2.50), or thick (≥2.50) and then placed

in paper bags (Figure 3).

The herbaceous plants within the frame area were

previously classified as weeds, lianas, shrubs, and forest

species, and the plants were quantified, measured for

maximum height up to 1.80 m, and identified according to

Lorenzi (2008). Then, the plants were uprooted with the

whole root system, weighed in the field to obtain the fresh

weight, and stored in labeled paper bags.

The samples of areas without fire (controls) were

collected parallelly at 10.0 m distant from each plot, in

interrows. In this case, five treatments were established:

control, native forest, and different post-fire periods: May

2015 (36 months), September 2015 (32 months), August

2016 (21 months).

The percentage of herbaceous plants and litterfall

differentiation in post-fire areas were determined through

photos taken from the sampling frame areas using an above

ground camera at 1.30 m height, with three replications/plots

for areas with prescribed fire and one replication for controls.

The images were evaluated in the Adobe Photoshop Cs6

program to determine the percentage, by counting the pixels

of the images (Figure 4).

The combustible matter collected was placed in forced

air-circulation oven, with temperature of 65±2 °C for 72

hours and then weighed in an analytical balance with

precision of 0.0001 g to assess its dry weight.

Figure 2. Environmental interfaces and frame used for the

collection of combustible matter after 36-months of controlled

post-fire in a Eucalyptus urograndis plantation in Sorriso, MT, Brazil.

Wherein: EA = Eucalyptus/Agriculture (a and d); EE = Eucalyptus/Eucalyptus (b

and d); EF = Eucalyptus/Forest (c and d).

Figura 2. Interfaces ambientais e quadrantes utilizados para a coleta

de material combustível em 36 meses de pós-queima controlada, em

plantio de Eucalyptus urograndis em Sorriso, MT, Brasil. Em que: (a) e (d)

Eucalyptus/Agriculture (EA); (b) e (d) Eucalyptus/Eucalyptus (EE); (c) e (d)

Eucalyptus/Forest (EF).

Figure 3. Classification of litterfall in Eucalyptus urograndis plantations

into: (a) leaves; (b) bark; (c) thin branches ≤0.7; (d) medium

branches (≥0.7 and ≤2.50); (e) thick branches (≥2.50); (f) storage of

the screened matter.

Figura 3. Triagem da serapilheira de Eucalyptus urograndis em classes:

(a) folhas; (b) casca; (c) galho fino ≤0,7; (d) galho médio (≥0,7 e

≤2,50); (e) galho grosso (≥2,50); (f) armazenamento do material

triado.

Figure 4. Percentages of the regenerated matter: (a) sampling frame

image; (b) image evaluation in the Adobe Photoshop Cs6 program;

percentage of green matter collected in the interfaces with Eucalyptus

urograndis plantations.

Figure 4. Quantificação do percentual de material regenerado: (a)

imagem do quadrante amostral; (b) imagem avaliada no Software

Adobe Photoshop Cs6; (c) especificações da estatística da imagem,

destaque em vermelho do percentual de material verde coletado nas

interfaces de Eucalyptus urograndis.

Camargo et al.

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2.4. Phytosociological analysis of the burnable

herbaceous plants

The following phytosociological variables of burnable

herbaceous plants were analyzed: frequency (F); relative

frequency (Fr); density (D), which enables to determine the

quantity of plants of each species per unit of area; relative

density (Dr); abundance (A); relative abundance (Air);

importance index (IVI) (Mueller-Dombois; Ellenberg, 1974)

and relative importance index (IVIr) (Braun-Blanquet, 1979).

The variables Fr, Dr, and Air shows information on the

relation between the species found in the area, and are used

to obtain the IVI (Sena et al., 2019).

2.5. Statistical analyses

The data of the inventory were subjected to analysis of

variance (ANOVA) in a 3×4 factorial arrangement consisted

of litterfall and regenerated herbaceous plants, and when the

means showed differences, the Tukey's test at 5% probability

level was applied, both using the Sisvar statistical program

(FERREIRA, 2011).

The herbaceous plants were subjected to inferential

analyses following the specificities of the variables,

considering the wealth, abundance, and presence/absence of

species in the plant community. The analyses were carried out

in the R environment. Graphics were developed using the R

basic packages, and the R ggplot2 package (WICKHAM,

2016).

The rarefaction curves and extrapolation of species to the

community were based on the series of Hill, using the

iNEXT package (HSIEH et al., 2019), and compared

considering the periods with and without fire and the EA and

EF interfaces. The rarefaction indicates the wealth observed

as a function of the sampling effort used, and the

extrapolation.

A general linearized mixed model (GLMM) was

developed to determine the variation in wealth as a function

of periods of post-fire and control (VENABLES; RIPLEY,

2002). This methodology was chosen due to the existing

argument in the function that corrects the spatial data with

possible effect of autocorrelation. Thus, the plots were used

as random variable in the model to control the spatial

autocorrelation. The test for statistical significance was

carried out by analysis of type II square deviations (FOX;

WEISBERG, 2019).

The ordering of species of the plant community by non-

metric multidimensional scaling was carried out for the

abundance analysis (OKSANEN et al., 2019). Abundance

data tend to present high variation, therefore, locations that

presented no occurrence were excluded before the analyses,

and the transformation of Hellinger (OKSANEN et al.,

2019) was applied to equal the variance, since the calculation

of distances in matrices of abundance does not admit zero

values.

The dimensional solutions for abundance and

presence/absence data were used as dependent variable in

the statistical model, since they represent the highest

recovered variability of the plant community (abundance: r2adj

= 0.46, p < 0.001; presence/absence: r2adj = 0.62, p < 0.001).

Multivariate models of analysis of variance were

developed to determine whether abundance and

presence/absence variations (represented by dimensional

solutions - NMDS) are associated with the post-fire, post-fire

period, or interface.

3. RESULTS

3.1. Plantation Inventory Analysis

The forest community evaluated was very homogeneous,

considering that all plants had the same age (6.5 years). The

effects of prescribed fire and forest and agriculture interfaces

on the growth and development of the eucalyptus plantation

was low.

Regarding the number of trees, a mean of 16 trees per

plot was found in the areas with and without fire, with no

significant difference between plots. No significant

difference in tree survival rate was found between the

controls and areas with fire for the interfaces EA, EE, and

EF by the Tukey's test (Table 1).

The survival rate in the community was high, with

minimum rate of 77.5% (32 months) and maximum of

93.75% (36 months), both in the EF interface. Regarding the

mortality rate, the areas with fire showed similar results to

areas without fire, with no significant difference between

environmental interfaces, nor between the periods with and

without fire. The maximum mortality found was 22.50% (32

months), and the minimum was 6.25% (36 months), both in

the EF interface.

Regarding the CBH, the performance of the forest

community showed increases as expected, considering the

age of the plant, differing statistically only in the EA interface,

with circumference of 51.83 cm for the 36-month post-fire

and 65.95 cm for areas without fire.

Table 1. Total number of trees, percentage of living and dead trees, circumference at breast height (CHC) Eucalyptus. urograndis (Clone H13)

plantations in three envirnomental interfaces over 21-, 32-, and 36-month post-fire periods and without fire (control), Sorriso, MT, Brazil.

Tabela 1. Número de árvores total, percentual de árvores vivas e morta, circunferência a altura do peito (CAP) em área de Eucalyptus urograndis

- Clone H13 em três interfaces com 21, 32, 36 meses pós-queima e sem queima, em Sorriso, MT, Brasil.

Period Number of trees Percentage of living (%) Percentage of dead (%) CBH (cm)

EA EE EF EA EE EF EA EE EF EA EE EF

21 15.67 Aa

17.33 Aa

16.33 Aa

82.98 Aa

80.77 Aa

81.63 Aa

17.02 Aa

19.23 Aa 18.37 Aa

59.39 ABa

59.50 Aa 61.32 Aa

32 16.00 Aa

20.00 Aa

13.33 Aa

89.58 Aa

78.33 Aa

77.50 Aa

10.42 Aa

21.67 Aa 22.50 Aa

61.58 ABb

55.58 Aab

51.81 Aa

36 14.33 Aa

17.33 Aa

10.67 Aa

81.40 Aa

90.38 Aa

93.75 Aa

18.60 Aa

9.62 Aa 6.25 Aa

51.83 Aa 53.25 Aa 56.91 Aa

Without

fire 15.33 Aa

16.67 Aa

14.33 Aa

86.96 Aa

82.00 Aa

81.40 Aa

13.04 Aa

18.00 Aa 18.60 Aa

65.94 Bb 58.32 Aab

51.83 Aa

wherein: EA (eucalyptus/agriculture); EE (eucalyptus/eucalyptus); EF (eucalyptus/ remnant of native forest). * Means followed by equal uppercase letters

in the column and lowercase in the row do not differ by Tukey's test at 5% probability.

em que: EA (eucalipto/agricultura); EE (eucalipto/eucalipto); EF (eucalipto/remanescente de floresta nativa). * Médias seguidas por letras iguais maiusculas

na coluna e minusculas na linha, não diferente entre si pelo teste de Tukey a 5% de probabilidade.

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The analysis of variance for commercial height showed

no significant differences between post-fire periods and

controls for the EA and EF interfaces, presenting higher

commercial heights when compared to trees in the center of

the parcel (EE). The EE interface showed different

commercial heights from the EA and EF interfaces for areas

with fire in the 36- and 21-month post-fire periods, and EE

and EF differed in areas without fire (Table 2).

The same result was found for total height; periods with

and without fire did not differ from each other in the EA and

EF interfaces, whereas for EE, the total height for the 21-

month post-fire period (30.90 m) were different from that of

areas without fire (36.88 m).

The percentage of occupation of canopy in the absence

of fire showed differences between environmental interfaces;

EF had higher percentage (72.67%), differing from EE (65%)

and EA (63%). In areas with fire, the interface EE differed

statistically from the EF interface (Table 2).

3.2. Combustible matter analysis - Litterfall

The analyses in areas with and without fire showed no

significant differences in litterfall accumulation between the

EA, EE, and EF interfaces by the Tukey's test. The mean

accumulation in control areas with 6.5 years of age were 23.61

Mg ha-1 (EA), 18.95 Mg ha-1 (EE), and 23.76 Mg ha-1 (EF),

denoting decreases in the center of the community (Table 3).

The highest accumulation rate in the period of 21-month

post-fire period was found for the EF interface (14.77 Mg ha-

1). In the 32- and 36-month post-fire periods, the EA

interface presented higher accumulation, 20.70 Mg ha-1 and

20.71 Mg ha-1, respectively.

Table 2. Commercial to total height ratio and percentage of occupation of canopy in Eucalyptus. urograndis (Clone H13) plantations in three

envirnomental interfaces over 21-, 32-, and 36-month post-fire periods and without fire (control), Sorriso, MT, Brazil.

Tabela 3. Altura comercial/total e percentual de ocupação de copa em área de Eucalyptus. urograndis (Clone H13) em três interfaces com 21,

32, 36 meses pós-queima e Sem Queima (testemunha), Sorriso, MT, Brasil.

Período Commercial height (m)

Total height (m)

Canpoy percentagem occupation (%)

EA EE EF

21 35.61 Ab 28.98 ABa

38.91 Ab

39.99 Ab

30.90 Aa 42.26 Ab

67.66 ABab

61.33 Aa 72.33 Ab

32 34.42 Aa 31.83 ABa

33.75 Aa

39.21 Aa

35.57 ABa

38.88 Aa

73.67 Bb 68.00 ABab

66.00 Aa

36 37.98 Ab 27.28 Aa 37.27 Ab

39.92 Ab

30.66 Aa 40.12 Ab

61.33 Aa 70.33 Bb 66.00 Aab

Without fire

35.17 Aab 32.52 Ba 37.97 Ab

40.39 Aa

36.88 Ba 39.92 Aa

63.00 Aa 65.00 ABa 72.67 Ab

wherein: EA (eucalyptus/agriculture); EE (eucalyptus/eucalyptus); EF (eucalyptus/ remnant of native forest). * Means followed by equal uppercase letters

in the column and lowercase in the row do not differ by Tukey's test at 5% probability.

em que: EA (eucalipto/agricultura); EE (eucalipto/eucalipto); EF (eucalipto/remanescente de floresta nativa). * Médias seguidas por letras iguais maiusculas

na coluna e minusculas na linha, não diferente entre si pelo teste de Tukey a 5% de probabilidade.

Table 4. Classes of combustible matter (Mg ha-1) in Eucalyptus. urograndis (Clone H13) plantations in three envirnomental interfaces over 21-

, 32-, and 36-month post-fire periods and without fire (control), Sorriso, MT, Brazil.

Tabela 5. Classes de material combustível (Mg ha-1) em áreas de E. urograndis (Clone H13) em três interfaces com 21, 32, 36 meses pós-

queima, e áreas Sem Queima (testemunha), em Sorriso, MT, Brasil.

Period

Interface

Leaf Bark T1 T2 T3 MH Total

EL 4.56 Aa 4.99 Aa 1.73 Aa 2.04 Aa 0.25 Ab 0.41 Aa 13.98 Aa

EE 4.74 Aa 4.02 Aa 1.72 Aa 1.71 Aa 0.00 Aa 0.00 Aa 12.19 Aa

EF 4.58 Aa 2.27 Aa 1.71 Aa 3.42 Aa 0.00 Aa 2.79 Bb 14.77 Aa

EL 6.93 ABa 4.94 Aa 3.88 ABa 4.70 Aa 0.00 Aa 0.23 Aa 20.70 Aa

EE 6.37 Aa 2.27 Aa 2.92 Aa 3.39 Aa 0.00 Aa 0.63 Aab 15.59 Aa

EF 6.35 Aa 3.19 Aa 2.54 Aa 3.89 Aa 0.00 Aa 2.09 ABb 18.05 Aa

EL 6.03 Aa 3.18 Aa 4.81 Bb 6.67 Aa 0.00 Aa 0.03 Aa 20.71 Aa

EE 7.04 Aa 5.13 Aa 3.57 Aab 4.13 Aa 0.00 Aa 0.00 Aa 19.88 Aa

EF 6.34 Aa 2.62 Aa 2.66 Ab 4.56 Aa 0.00 Aa 2.05 ABb 18.22 Aa

Without fire

EL 11.26 Ba 3.72 Ab 4.44 Bb 4.13 Aab 0.00 Aa 0.06 Aa 23.61 Ab

EE 7.26 Aa 3.27 Ab 3.70 Ab 4.72 Aab 0.00 Aa 0.00 Aa 18.95 Aab

EF 9.19 Aa 3.01 Aab 3.36 Aab 7.64 Ab 0.00 Aa 0.56 Aa 23.76 Ab

wherein: EA (eucalyptus/agriculture); EE (eucalyptus/Eucalyptus); EF (eucalyptus/ remnant of native forest); T1 = thin branches with diameters (d) < 0.7

cm; T2 = medium branches 0.7 < (d) < 2.5 cm; T3 = thick branches (d) > 2.5 cm); EP = herbaceous plants, Mg ha-1 = megagrams per hectare. *Means

followed by the same uppercase letter in the columns or lowercase letter in the rows are not different from each other by the Tukey's test at 5% probability

level.

em que: EA (eucalipto/agricultura); EE (eucalipto/eucalipto); EF (eucalipto/remanescente de floresta nativa); T1: galhos finos diâmetro (d) < 0,7 cm); T2:

galhos médios 0,7 < (d) < 2,5 cm; T3 grossos (d) > 2,5 cm); MH. (Material Herbáceo), Mg ha-1 (megagramas por hectare). * Médias seguidas por letras iguais

maiusculas na coluna e minusculas na linha, não diferente entre si pelo teste de Tukey a 5% de probabilidade.

Leaves represented the highest fraction among the

litterfall classes, since areas without fire presented higher

deposition, standing out the EA interface, with 11.26 Mg ha-

1, representing 47.69% of all combustible matter (Figure 5a),

differing from the EE (7.26 Mg ha-1 / 38.31%) (Figure 5b)

and EF (9.19 Mg ha-1 / 38.68%) (Figure 5c) interfaces; EE

and EF were not different from each other.

A higher percentage of occurrence of the bark class was

found in the 21-month post-fire period in the EF (32.62%)

and EE (38.88%) interfaces (Figures 5a and b). No significant

difference in bark deposition after the fire was found by

Tukey’s test, presenting means (21-, 32-, and 36-month post-

fire periods) of 4.36 Mg ha-1 (EA); 3.81 Mg ha-1 (EE), and

2.69 Mg ha-1 (EF). These results were similar those in the

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153

control period, which were 3.72 for EA, 3.27 for EE, and

3.01 Mg ha-1 for EF.

Thin branches were not much representative; however,

similar results were found for the EA interface between the

36-month post-fire period (4.81 Mg ha-1) and without fire

(4.44 Mg ha-1). Thick branches were found only in the EA

interface in the 21-month post-fire period, with 0.25 Mg ha-

1, representing 1.79% (Figure 5a).

The regeneration of herbaceous plants was lower when

compared to the litterfall class. The interface that presented

the highest regeneration percentage was the EF (Figure 5c),

with 18.89% (21 months), 11.58% (32 months) and 11.25%

(36 months). The regeneration in the EE interface occurred

only in the 32-month post-fire period. The proportion of

herbaceous plants was low in the controls, and was found in

the EA (0.25%) and EF (2.35%) interfaces, which did not

differ statistically from each other (Table 3).

The total deposition of combustible matter in the

remaining native forest fragment next to the eucalyptus

community was 13.66 Mg ha-1, with no significant difference

when compared to the total litterfall deposition of the E.

urograndis plantation (22.11 Mg ha-1) with 6.5 years of age.

Bark and thick branch depositions did not occur in the forest,

leaf deposition presented the highest fraction in the total

mean accumulation of combustible matter, with 9.92 Mg ha-

1, representing of 72.62% (Table 4 and Figure 6).

Figure 6. Class distribution of litterfall in Eucalyptus urograndis (Clone

H13) plantations and in a native forest fragment in the Cerrado-

Amazon transition in Sorriso, MT, Brazil. wherein: G1 = thin

branches with diameters (d) < 0.7 cm); G2 = medium branches 0.7

< (d) < 2.5 cm; G3 = thick branches (d) > 2.5 cm); EP = herbaceous

plants.

Figura 6. Distribuição da serapilheira por classes na floresta plantada

de Eucalyptus urograndis (Clone H13) e na Floresta Nativa

remanescente transição Cerrado-Amazônia, em Sorriso - MT. em

que, T1: galhos finos diâmetro (d) < 0,7cm); T2: galhos médios 0,7

< (d) < 2,5 cm; T3 grossos (d) > 2,5 cm); MH - Material Herbáceo.

Figure 5. Distribution of litterfall by classes within the interfaces eucalyptus/agriculture (a), eucalyptus/eucalyptus (b), and eucalyptus/

remnant of native forest (c) in areas with Eucalyptus urograndis (Clone H13) plantations in Sorriso, MT, Brazil, with different controlled post-

fire periods (21, 32, and 36 months) and without fire (77 months of age). wherein: T1 = thin branches with diameters (d) < 0.7 cm); T2 =

medium branches 0.7 < (d) < 2.5 cm; T3 = thick branches (d) > 2.5 cm); MH = herbaceous plants.

Figura 5. Distribuição da serapilheira por classes nas interfaces (a) eucalipto/agricultura; (b) eucalipto/eucalipto; (c) eucalipto/remanescente

de floresta nativa, das áreas de Eucalyptus urograndis (Clone H13) em Sorriso, MT, Brasil, com diferentes períodos pós-queima controlada (21,

32 e 36 meses), e sem queima (77 meses – idade do plantio). em que: as classes foram descritas como: T1: galhos finos diâmetro (d) < 0,7

cm); T2: galhos médios 0,7 < (d) < 2,5 cm; T3: galhos grossos (d) > 2,5 cm); MH (Material Herbáceo).

Table 6. Dry masso f the classes of combustible matter (Mg ha-1) in areas with E. urograndis (Clone H13) plantations and in a remnant of

native forest in Sorriso, MT, Brazil.

Tabela 7. Massa seca das classes de material combustível (Mg ha-1) em áreas de E. urograndis (Clone H13) e em um remanescente de floresta

nativa, em Sorriso, MT, Brasil.

Area Leaf Bark T1 T2 T3 MH Total

Eucalyptus urograndis 9.24 Aa 3.34 Aa 3.83 Aa 5.50 Aa 0.00 Aa 0.21 Aa 22.11 Aa

Forest 9.92 Aa 0.06 Aa 1.17 Aa 2.10 Aa 0.00 Aa 0.39 Aa 13.66 Aa

3.3. Combustible matter analysis - regenerated

herbaceous plants

The surveying of regeneration of green biomass in the

three interfaces in the post-fire periods and in the control

period (77 months) totalized 120 individuals, distributed into

17 genus, and one indeterminate, from 9 botanical families

(Table 5 and Figure 7). The regeneration of herbaceous plants

in post-fire areas was higher in the EA and EF interfaces,

predominating grass species from the Poaceae family,

whereas the bushy plants were more representative in the

areas without fire. Four species of the Poaceae family were

found in the experimental area, namely, Panicum maximum,

Paspalum maritimum, Panicum pernanbucensis, and Brachiaria

decumbens. P. maritimum presented higher abundance in all

interfaces and periods with and without fire (Figure 7a). The

more frequent species in the 21-month post-fire period in the

Litterfall and herbaceous plants regeneration in planted forests at post prescribed fire …

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154

interface EA was Machaerium sp. (33.3%); P. maritimum

(29.6%) presented the highest IVIr (Table 5). P. maximum and

P. maritimum represented more than half of all population

present in the EF interface, with frequency of 53.8%; P.

maximum presented the highest IVIr, with 38.3%. The

samples of the EE interface showed no regeneration of

herbaceous plants.

Table 5. Statistical variables of occurrence of regenerated species in areas with Eucalyptus urograndis (Clone H13) plantations post prescribed

fire in different environmental interfaces in Sorriso, MT, Brazil.

Tabela 5. Variáveis estatísticas da ocorrência de espécies regeneradas em áreas de Eucalyptus urograndis (Clone H13) pós-queimas prescritas

em diferentes interfaces ambientais, em Sorriso, MT, Brasil.

Burn Interface Period Specie Family Popular name Fr Dr Ar IVIr

(%)

Yes EL 21

Machaerium sp. Fabaceae Cipó 33.3 26.7 26.7 28.9

Panicum maximum Poaceae Capim-mombaça 22.2 13.3 13.3 16.3

Melampodium divaricatum Asteraceae Flor-amarela 11.1 6.7 6.7 8.1

Paspalum maritimum Poaceae Capim-pernambuco 22.2 33.3 33.3 29.6

Brachiaria decumbens Poaceae Brachiaria 11.1 20.0 20.0 17.0

Yes EF 21

Panicum maximum Poaceae Capim-mombaça 26.9 44.0 44.0 38.3

Paspalum maritimum Poaceae Capim-pernambuco 26.9 26.7 26.7 26.8

Blainvillea biaristata Asteraceae Picão 7.7 6.7 6.7 7.0

Melampodium divaricatum Asteraceae Flor-amarela 15.4 10.7 10.7 12.2

Mezilaurus itauba Fabaceae Itaúba 7.7 2.7 2.7 4.3

Machaerium sp. Fabaceae Cipó 15.4 9.3 9.3 11.4

Yes EL 32

Machaerium sp. Fabaceae Cipó 16.7 4.3 4.3 8.5

Paspalum maritimum Poaceae Capim-pernambuco 33.3 43.5 43.5 40.1

Melampodium divaricatum Asteraceae Flor-amarela 33.3 13.0 13.0 19.8

Panicum maximum Poaceae Capim-mombaça 16.7 39.1 39.1 31.6

Yes EE 32 Paspalum maritimum Poaceae Capim-pernambuco 100.0 100.0 100.0 100.0

Yes EF 32

Panicum maximum Poaceae Capim-mombaça 15.0 23.7 23.7 20.8

Rumex crispus Polygonaceae Paciência 10.0 6.8 6.8 7.9

Brachiaria decumbens Poaceae Brachiaria 10.0 13.6 13.6 12.4

Indeterminado

10.0 3.4 3.4 5.6

Paspalum maritimum Poaceae Capim-pernambuco 30.0 42.4 42.4 38.2

Solanum paniculatum Solanaceae Jurubeba 10.0 3.4 3.4 5.6

Vismia guianensis Hypericaceae Lacre-branco 5.0 1.7 1.7 2.8

Melampodium divaricatum Asteraceae Flor-amarela 5.0 3.4 3.4 13.6

Croton lobatus Euphorbiaceae Café-bravo 5.0 1.7 1.7 2.8

Yes EL 36

Melampodium divaricatum Asteraceae Flor-amarela 27.3 16.7 16.7 15.9

Panicum permanbucensis Poaceae Palha-branca 9.1 11.1 11.1 8.2

Panicum maximum Poaceae Capim-mombaça 9.1 5.6 5.6 5.3

Spermacoce palustres Rubiaceae Erva-de-lagarto 9.1 5.6 5.6 5.3

Machaerium sp. Fabaceae Cipó 27.3 44.4 44.4 30.4

Paspalum maritimum Poaceae Capim-pernambuco 18.2 69.7 134.6 17.2

Yes EE 36 Paspalum maritimum Poaceae Capim-pernambuco 100.0 100.0 100.0 100.0

Yes EF 36

Solanum paniculatum Solanaceae Jurubeba 13.0 5.4 5.4 7.9

Brachiaria decumbens Poaceae Brachiaria 26.1 51.8 51.8 43.2

Melampodium divaricatum Asteraceae Flor-amarela 4.3 1.8 1.8 2.6

Rumex crispus Polygonaceae Paciência 13.0 5.4 5.4 7.9

Blainvillea biaristata Asteraceae Picão 4.3 7.1 7.1 6.2

Paspalum maritimum Poaceae Capim-pernambuco 4.3 3.6 3.6 3.8

Panicum maximum Poaceae Capim-mombaça 8.7 3.6 3.6 5.3

Mezilaurus itauba Fabaceae Itaúba 8.7 5.4 5.4 6.5

Machaerium sp. Fabaceae Cipó 8.7 3.6 3.6 5.3

Spermacoce palustres Rubiaceae Erva-de-lagarto 4.3 7.1 7.1 6.2

lmperata brasiliensis Panicoideae Sapê 4.3 5.4 5.4 5.0

No EL 77 Spermacoce palustres Rubiaceae Erva-de-lagarto 50.0 75.0 75.0 66.7

Machaerium sp. Fabaceae Cipó 50.0 25.0 25.0 33.3

No EF 77

Paspalum maritimum Poaceae Capim-pernambuco 18.2 21.6 21.6 20.5

Mezilaurus itauba Fabaceae Itaúba 13.6 8.1 8.1 10.0

Melampodium divaricatum Asteraceae Flor-amarela 27.3 35.1 35.1 32.5

Rumex crispus Polygonaceae Paciência 4.5 2.7 2.7 3.3

Ageratum conyzoides Asteraceae Picão-roxo 4.5 2.7 2.7 3.3

Machaerium sp. Fabaceae Cipó 13.6 8.1 8.1 10.0

Cyperus iria Cyperaceae Tiririca 4.5 13.5 13.5 10.5

Scleria melaleuca Cyperaceae Campim-navalha 4.5 2.7 2.7 3.3

Panicum maximum Poaceae Capim-mombaça 4.5 2.7 2.7 3.3

Brachiaria decumbens Poaceae Brachiaria 4.5 2.7 2.7 3.3

wherein: EA (eucalyptus/agriculture), EE (eucalyptus/eucalyptus - central interface of the eucalyptus parcel); EF (eucalyptus/remnant of native forest); Fr

= relative frequency; Dr = relative density; Air = relative abundance; IVIr = Relative Importance Index.

em que: EA (eucalipto/agricultura), EE (parcela interface centro do talhão do eucalipto – eucalipto/eucalitpto) e EF (parcela interface

eucalipto/remanescente de floresta nativa); Fr (Frequência Relativa); Dr (Densidade Relativa); Ar (Abundância Relativa); IVIr (Índice de Valor de Importância

Relativo).

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155

The most abundant species found for the 21-month post-

fire period was, in general, P. maximum, regardless of the

interface (Figure 7b). The 21-month post-fire period

presented higher occurrences of regeneration for EA and EF.

The most representative species found for 32-month post-

fire period in the EA interface was P. maritimum, with IVIr of

40.1%; this species presented the highest density and

abundance. Grouping the post-fire periods, the species P.

maritimum represented 100% (RF and IVIr) in the EE and

30% (RF) and 38.2% (IVr) in EF; thus, it can be described as

the most abundant species for the 32-month post-fire period

(Figure 7c).

Figure 7. Distribution of abundance as a function of sampled plant

species. Abundance is in logarithmic scale for a better view of the

community standard. The relations presented are: total community

(a), 21, 32-, and 36-month post-fire periods (b a d, respectively),

without fire for 77 months (e); and interfaces eucalyptus/agriculture

– EA (f) and eucalyptus/remnant of native forest– EF (g).

Figura 7. Distribuição da abundância em função das espécies

vegetais amostradas. Abundância está em escala

logarítmica para melhor visualizar o padrão da comunidade. As

relações apresentadas são: comunidade total (a), períodos pós-

queima de 21, 32 e 36 meses (b a d, respectivamente), sem queima

– 77 meses (e); e ainda, para interfaces eucalipto/agricultura (EA),

(f) e eucalipto/remanescente de floresta nativa (EF) (g).

Consequently, higher diversity of species was found for

the 36-month post-fire period; Machaerium sp. presented the

highest representativeness in the EA interface, with IVIr of

30.4%; only P. maritimum was found in the EE interface, with

100% frequency and IVIr; the grass species B. decumbens

presented the highest representativeness among the plants

sampled in the EF interface, with 26.1% frequency and

43.2% IVIr (Table 5). The most abundant species found for

the 36-month post-fire period was B. decumbens (Fig. 7d).

The species Spermacoce palustre and Machaerium sp. were

found in areas without fire and in the interface EA, with 50%

frequency and 66.7% and 33.3% IVr, respectively (Table 5).

The species with higher frequency in the EF interface was

Melampodium divaricatum, with 27.3% frequency and 32.5%

IVr. No species was found in the interface EE. Considering

the areas without fire, the most abundant species was M.

divaricatum (Figure 7e). When comparing the regeneration of

herbaceous plants in the interfaces, EA presented lower

regenerated plants than EF (Figure 7f-g).

The regeneration of herbaceous plants was higher in the

EF interface, regardless of the post-fire period (Figure 8);

higher proportions were found for the 21-month post-fire

period, with 55.4% for litterfall and 44.6% for regenerated

herbaceous plants.

The rarefaction curves developed showed lower wealth

of species in areas without fire and higher wealth in areas with

controlled fire (Figure 9). The post-fire periods and control

affected the abundance variation in the plant community and

the presence/absence was also affected by the community

interface (Table 6).

The similarity between areas with fire was low for the

regeneration of herbaceous plants, abundance, and

presence/absence (Figure 10). Similar results were also found

for post-fire periods and control, and community interfaces.

Figure 8. Percentage of area occupied by litterfall and herbaceous plants by post prescribed fire period. (a) EA [eucalyptus/agriculture]; (b)

EE [eucalyptus/eucalyptus – center of the parcel]; (c) EF [eucalyptus/remnant of native forest].

Figura 8. Percentual de área ocupada por serapilheira e material herbáceo por tempo pós-queimas controladas. (a) EA [eucalipto/agricultura];

(b) EE [eucalipto/eucalipto – centro do talhão]; (c) EF (eucalipto/remanescente de floresta nativa].

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156

Figure 9. Wealth of plant species found (continuous line) and extrapolated wealth (dotted line) as a function of the sample effort. Rarefaction

curves and extrapolations were calculated for (a) treatments with fire, (b) post-fire period, control without fire (77 months), and (c) interfaces

of the community. The shaded area represents the confidence interval.

Figura 9. Relação da riqueza de espécies vegetais observada (linha contínua) e riqueza extrapolada (linha pontilhada) em função do esforço

amostral. As curvas de rarefação e extrapolação foram calculadas para (a) tratamento de queima, (b) período pós-queima e testemunha (sem

queima – 77 meses), bem como (c) interfaces do povoamento. A área sombreada representa o intervalo de confiança.

Figure 10. Tridimensional spatial distribution of samples of abundance (Bray-Curtis distance) (a, c, e) and presence/absence of herbaceous

plants (Sørensen distance) (b, d, f), as a function of post-fire periods (a, b), post-fire period and control (c, d), and interface of the community

(e, f) in a E. urograndis (Clone H13) plantation.

Figure 10. Distribuição tridimensional das amostras no espaço da abundância (distância de Bray-Curtis) (a, c, e) e presença/ausência de

material herbáceo (distância de Sørensen) (b, d, f), em função dos períodos pós-queima (a, b), período pós-queima e testemunha (c, d) e

interface do povoamento (e, f) em área de E. urograndis (Clone H13).

Table 6. Probabilities associated to the abundance and presence/absence (represented by dimensional solutions - NMDS) variables as a

function of fire, post-fire periods, control, and interface of the community.

Tabela 6. Probabilidades associadas das variáveis abundância e presença/ausência (representadas pelas soluções dimensionais do NMDS)

em função de queima, períodos de pós-queima e controle (testemunha), e interface do povoamento.

Source of variation Abundance (NMDS)

Presence/Absence (NMDS)

gL Pillai-Trace P

Burn* 1 0.028 0.524

1 0.035 0.446

Post

burn period and

control

2 0.311 0.003

2 0.232 0.020

Settlement interface

2 0.149 0.118

2 0.205 0.036

Burn*Interface

1 0.077 0.113

1 0.029 0.508

Period*Interface

3 0.146 0.296

3 0.037 0.938

Waste

* Considering only the occurrence of fire, regardless of the post-fire period.

* Considerando apenas a ocorrência de queima, independentemente do período pós-queima.

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157

4. DISCUSSION

4.1. Forest inventory

The prescribed fire had no effect on the community

development, since the survival rate of trees was higher than

77%. This is connected to the low to moderate intensity of

prescribed fires on the surface of the sub-forest, which

seldom cause mortality of large-size trees (NOSS et al., 2006).

Studies with E. urograndis presented high survival rates,

varying from 91.8 to 95.9% in Roraima, and mortality rate of

18.92% in Mato Grosso (TONINI, 2006; MIRANDA et al.,

2019).

The mortality of eucalyptus tends to increase in plants

with age higher than 7 years, however other variables can be

associated, such as soil nutrition, weather conditions, water

availability, species adaptation, and inadequate silvicultural

practices (CAMPOE et al., 2016; CARMO et al., 2018;

MIRANDA et al., 2019).

Considering that the community analyzed had 6.5 years

of age, it was within the expected standards for survival rates

and mortality. Significant difference was found for CHC only

for the EA interface; however, this variation is common in

monospecific agriculture (VIERA et al., 2011). Therefore, it

was considered as normal for this age, since CHC and height

variables affect the wood volume, thus ensuring more

profitability in wood production for generation of energy.

The tree heights in the center of the community varied,

which is connected to the lower solar radiation incidence in

the center of the parcel; the trunk length growth depends on

light availability and trees in shading conditions tend to have

lower heights or be suppressed (BINKLEY et al., 2010).

Canopy percentage is also important for this study, since

the higher the canopy percentage, the lower the solar

radiation incidence (Viera et al., 2011) in the sub-forest. It can

affect the regeneration of herbaceous plants and decrease the

combustible matter availability. Thus, the application of

prescribed fire to the litterfall of the parcel is not a threat for

the plantation development. The mean values of variables

surveyed for the post-fire periods are similar those found in

the control.

4.2. Combustible matter - litterfall

The litterfall in areas with H13 clone are composed of

leaves, barks, thin branches, medium branches, and

herbaceous plants. The deposition of combustible matter

was, in general, similar in all interfaces, post-fire periods, and

areas without fire, showing that border and central areas of

the community do not affect the combustible matter

production, and the accumulation increases and tend to be

constant after 36 months. This similarity can be correlated

with the biomass decomposition, which is slow for

eucalyptus litterfall (SCHUMACHER et al., 2013).

The area without fire reached a maximum litterfall

production of 23.7 Mg ha-1 at 6.5 years of age; however, the

plantation cut cycle is between 7 and 7.6 years, thus, it stops

this combustible matter deposition. However, there are a risk

of fire before cutting, since combustible matter depositions

of 8 to 12 Mg ha-1 are high, 12 to 20 Mg ha-1 are very high,

and > 20 Mg ha-1 are extreme (MARSDEN-SMEDLEY,

2011).

Regarding the classification, leaves represented the

highest fraction of the litterfall combustible matter in all

interfaces and periods with and without fire. Previous studies,

when the forest community presented 5 years of age

(CARMO et al., 2018), found that the leaf fraction was also

the main litterfall formation fraction, varying from 51.76%

(EF) to 60.99% (EE). It still presented 40.0% of leaves at 6.5

years of age (LIMA et al., 2020a,b). Other studies state that

the leaf fraction stands out in the litterfall composition

(NETO et al., 2014; INKOTTE et al., 2015; SANTOS et al.,

2017), confirming the data found in the present study.

Although species of the Eucalyptus genus have several leaf

predators, they are grown in abundance, favoring fire

propagation, that threatens the plantation (SCHNEIDER,

2003). Thus, the adoption of controlled fire is required when

the area reach high leaf loads (> 0.7 cm) (MARSDEN-

SMEDLEY, 2011).

Barks are composed of dead tissues; its purpose is to

protect and provide resistance to plants and a defense against

abiotic and biotic threats (FERRENBERG; MITTON, 2014;

PAUSAS, 2015). The prescribed fire did not cause stress in

the trees, since the bark quantity in areas with fire were similar

that in areas without fire.

Regarding the branch classes, which present low

deposition, those with thickness < 0.7 cm were little

representative, whereas those > 2.5 cm presented higher

deposition in EA, representing 1.79% of deposition total of

litterfall. Thus, branches with equal or lower thickness than

this do not significantly affect fire propagation (MARSDEN-

SMEDLEY, 2011).

The regeneration of herbaceous plants in areas without

fire was lower than that in areas with fire, presenting higher

regeneration next to the agriculture and forest borders. Other

studies found similar results and attributed the absence or

presence of herbaceous plants due to the light availability,

which is higher in border areas (CIANCIARUSO et al., 2010;

DEVECCHI et al., 2020). Fire can be beneficial to stimulate

or facilitate several developmental phases of many of these

species, mainly herbaceous plants (WROBLESKI;

KAUFFMAN, 2003).

The combustible matter availability in the planted and

native forest presented no significant difference regarding the

litterfall deposition. However, the plantation age was close to

the cutting time and the mature native forest age was not

determined, denoting that eucalyptus plantations have high

deposition of combustible matter and had no enough time

for the decomposition of this matter due to its short cycle.

4.3. Regenerated burnable herbaceous plants

Fire can favor the reproduction of grass species from the

Poaceae family, whereas it does not favor bush species, since

it delays the regeneration time (CIANCIARUSO et al., 2010).

Although grass species present high number of leaves, alive

plants are not threat, since the higher the quantity of green

matter, the lower the fire propagation (ALVES et al., 2017).

However, it should be noted that the behavior of grasses does

not always follow what is exposed in this work, making it

possible to burn areas with this type of vegetation, even in

the rainy season, due to the large amount of combustible

material deposited below the green leaves. Furthermore, in

dry periods, they become highly flammable, increasing the

risk of fires and present higher temperatures over longer

times (GORGONE-BARBOSA et al., 2016).

Grass species have efficient photosynthetic performances

for the production and dispersion of diaspores and are highly

invasive (SOUZA et al., 2005; GORGONE-BARBOSA et

al., 2016). For example, P. maritimum is a species with high

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158

capacity of invade crop areas, form homogeneous colonies,

dominating the area over few years, and preventing the

regeneration and development of other species (SOUZA

FILHO, 2006).

The 21-months post-fire period presented higher

regeneration for EA and EF, since the germination of lianas,

herbaceous plants, and grass species in the first months after

the controlled fire can be due to the overcoming of dormancy

of seeds present in the litterfall and in the soil. These plants

present ecological succession characteristics typical of

pioneer species, with fast growth and development, and short

life cycle (Ricklefs, 2003), which explains the high occurrence

of these plants in sampled areas close to the forest and their

survival time in the area.

The most abundant species in areas without fire was M.

divaricatum; thus, fire can be beneficial for herbaceous plants,

by stimulating or facilitate several phases of their

development, and alter soil fertility (WROBLESKI;

KAUFFMAN, 2003; SILVA; BATALHA, 2008) found

higher organic matter, nitrogen, and clay contents in areas

with fire occurrences, which are rapidly absorbed by grass

species with shallow roots (CIANCIARUSO et al., 2010);

thus, this is probably one of the reasons for the abundance

of grass species in areas with controlled fire.

The regenerated herbaceous plants covered a larger area

in the EF interface, regardless of the post-fire period. This is

probably due to the presence of the native forest fragment in

the border of the eucalyptus plantation and the higher water

availability than in the other interfaces due to the proximity

with a lake. The regeneration in the EE interface was low in

the three periods analyzed because of the lowest seed

dispersion and the lower solar radiation in the center of the

parcel.

5. CONCLUSIONS

The eucalyptus plantations in the Cerrado-Amazon

transition region subjected to prescribed fire presented, after

36 months, presented similar litterfall quantity and

composition to areas without fire (77 months).

Leaves represented the highest combustible matter

fraction (litterfall) followed by medium branches, barks, thin

branches, herbaceous plants, and thick branches. This

accumulation over time can favor the intensity and

propagation of fire.

Thus, prescribed fire can be an important tool for the

managing of dry and alive combustible matter in sub-forest

of eucalyptus plantations in this transition region after four

years of implementation by decreasing the litterfall surface

layer, considering the state legislation, thus allowing the

prevention of forest fires of large proportions.

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Acknowledgments:

The Coordenação de Aperfeiçoamento de Pessoal de Nível

Superior (CAPES) for awarding the scholarship (Process

88882.459210/2019-01). The National Scientific and Technological

Development Council (Conselho Nacional de Desenvolvimento

Científico e Tecnológico – CNPq) for the resources of the Research

Productivity Scholarship. To the members of the Research Group

"Environment and Plant Interactions". The Brasil Foods Company

(Lucas do Rio Verde Unit) for the release of the experimental area

and all UPL 03 employees.

Author Contributions: A.P.S.O.C. – field data collection,

laboratory analysis, statistical analysis, initial writing; D.C.L. and

J.F.K. – field data collection; R.A. - statistical analysis; A.P.S. -

conceptualization, methodology, research, validation, writing draft.

All authors read and agreed to the published version of the

manuscript.

Funding: Not applicable.

Institutional Review Board Statement: Not applicable.

Informed Consent Statement: Not applicable.

Data Availability Statement: Raw and analysed data can be

obtained by request to the corresponding Author by e-mail.

Conflicts of Interest: The authors declare that there is no conflict

of interests regarding the publication of this paper.