**[Broomsedge Burn]{.underline}**

**[Hawai\`i Volcanoes National Park]{.underline}**

**[Burned Area Emergency Rehabiltation Final Accomplishment
Report]{.underline}**

**National Park Service**

**December 15, 2004**

**Prepared by:**

**Rhonda Loh, Botanist, Hawaii Volcanoes National Park**

**Alison Ainsworth, David Benitez, Sierra Mcdaniel,**

**Matthew Schultz, Kimberly Smith, Tim Tunison, Maya Vaidya**

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  ![](media/image1.jpeg){width="5.35in" height="4.0125in"}

  Community volunteers broadcasting native seeds in the Broomsedge Burn,
  Fall 2000 (photo by Loh)
  -----------------------------------------------------------------------

**[Executive Summary]{.underline}**

The Broomedge Fire, started June 30, 2000, burned 1008 acres of native
plant communities (3,800-4,100 ft elevation) in Hawaii Volcanoes
National Park. The communities affected were seasonally dry \`ohi\`a
woodland (923 ac) and mesic koa forest (85 ac). Fire is expected to
dramatically reduce fire-sensitive native vegetation and stimulate
fire-adapted alien grasses, thereby increasing fire potential in the
burn area. Two strategies were used to revegetate burned communities.
The strategy in former seasonally dry \`ohi\`a (*Metrosideros
polymorpha*) woodlands (923 ac) was to establish a community of
fire-tolerant native species that could co-exist with alien grasses and
wildfire. The strategy in fire damaged mesic koa (*Acacia koa*) forest
(85 ac) was to increase fire resistance in specific sites by rebuilding
the structure of the native understory thereby reducing the risk of
wildfire spreading into high priority areas. This same strategy, to
increase fire resistance by establishing a thick understory beneath a
strip of koa forest, was used to reduce the likelihood of fire carrying
between the Park and private landowners in the nearby Volcano Golf
Course Subdivision. Restoration efforts began one week after the fire
and continued to 07/08/03. Approximately three thousand worker days,
including 1,239 volunteer days, were spent completing the project.
Thirty native plant species were established in the burn by a
combination of seeding \>2.7 million seeds and outplanting 18,798
individuals that were propagated in park temporary greenhouses. Along
with revegetation, workers searched and removed aggressive alien woody
species (e.g. *Myrica faya, Psidium cattleianum, Rubus argutus*) in
order to prevent their establishment in the burn. Over 7,400 individuals
were discovered and chemically or manually eradicated. Permanent
monitoring plots were established and the vegetation measured to
evaluate the success of the project. Average survivorship of outplants
in the plots was \>80% (all species). There was significant recruitment
of four species (*Acacia koa, Bidens hawaiiensis, Dodonaea viscosa,
Sophora chrysophylla*) from seed additions into the burn. By 2004,
eleven re-introduced native species had reached reproductive maturity in
the burn, including four tree, three shrub, a lily, Hawaiian poppy, and
two grass species. Monitoring will continue over the next few decades to
evaluate long term successional outcomes as a result of the restoration
project. The successful establishment of species by outplanting and
artificial seeding in the Broomsedge Burn serves as a model for
restoration in other fire-affected dry \`ohi\`a woodlands in the Park.

**[Table of Contents]{.underline}**

**[Page]{.underline}**

Executive Summary ii

Introduction 1

Methods 2

Native Plant Restoration 2

\`ohi\`a woodlands 2

Mesic koa forest 3

Koa stands 3

Seed collection, storage, propagation 3

Alien Plant Control 4

Monitoring Plant Community Response 4

Data analysis 4

Results 5

Native Plant Restoration 5

Alien Plant Control 6

Plant Community Response to Fire 6

Discussion 7

Native Plant Establishment from Outplanting

and Seeding 7

Prevention of Alien Woody Plant Establishment 8

Natural Recovery of the Preburn Community 8

Conclusion 8

Literature Cited 11

**[Table of Figure]{.underline}**

Table 1. Native species for introduction into

burned communities. 13

Table 2. Number of outplants and seeds added to the burn

by species. 14

Table 3. Outplant survivorship in the \`ohi\`a woodland site 15

**[Table of Figure]{.underline}**

######### Figure1. Map of plant communities affected by the

#########  Broomsedge Burn. 16

#########  

###### Figure 2. Seedling recruitment from seed addition 

into the burned \`ohi\`a woodland site (indiv/plot). 17

Figure 3. Native and exotic plant abundance three years

after the Broomsedge Burn. 18

**[Introduction]{.underline}**

The Broomedge Fire, started June 30, 2000, burned 1008 acres of native
plant communities (3,800-4,000 ft elevation) in Hawai\`i Volcanoes
National Park (HAVO) (Figure 1). Communities affected were seasonally
dry \`ohi\`a woodland (923 ac) and mesic koa forest (85 ac). Fire was
expected to dramatically reduce native vegetation and stimulate
fire-adapted alien grasses, thereby increasing fire potential in the
burn area (D\`Antonio and Vitousek1992 al, Tunison *et al.* 1995,
D\`Antonio *et al.* 2000). Two strategies were used to re-vegetate the
burned communities with native plants. A third strategy to prevent the
establishment of ecologically disruptive alien woody species was also
included in the rehabilitation plan.

The strategy in burned \`ohi\`a (*Metrosideros polymorpha*) woodlands
(\~900 acres) was to establish fire-tolerant native plants that could
persist in competition with exotic grasses and recurrent wild fires.
Since the invasion of fire-adapted invasive broomsedge (*Andropogon
virginicus*) and bushy beardgrass (*Schizachyrium condensatum*) in the
mid-1960\'s and molasses grass (*Melinis minutiflora*) in the 1970\'s,
fire frequency has increased three-fold, and fire size 60-fold. Nearly
two-thirds of the dry \`ohi\`a woodland system has been affected by
wildfire and the remaining portions are at high risk for wildfire at
HAVO. Re-introduction of formerly dominant but fire-sensitive native
plants such as \`ohi\`a, and pukeawe was considered counterproductive
given the widespread abundance of alien grasses that increased fuel
loads and thereby the inevitability of future fires (D\`Antonio and
Vitousek 1992). Instead, the intent was to create modified native
communities that were able to self-perpetuate, accepting that alien
grasses and wild fire remained important ecosystem components. Between
1993-2001, seven research burns and laboratory experiments were
conducted to test native species capacity to survive and colonize after
fire. Fourteen native plant species, among them mamane (*Sophora
chrysophylla),*a tree*,* \`a\`ali\`i *(Dodonaea viscosa*), a shrub,
and\` ili\`ahi (*Santalum ellipticum* var. *paniculatum*), a tree, were
identified as fire-tolerant (Loh et al. unpubl.). Additional species
were identified based on their ability to survive or colonize after
natural fire. Many of these species were formerly abundant in the
seasonally dry \`ohi\`a lowland ecosystem, but were depleted by historic
browsing by feral goats. Park boundaries were fenced from sea level to
6,600 ft elevation and goats removed in the 1970\`s. However, natural
recovery of species was poor because the native seed bank has been
depleted, and seedlings that did establish had a difficult time growing
in competition with alien grasses (Hughes and Vitousek 1993, D\`Antonio
*et al*.1998). Restoration in the Broomsedge Fire focused on
establishing 14 of these fire-tolerant native species by a combination
of seeding and outplanting of nursery-propagated individuals in the burn
(Table 1). The intent was to establish species rapidly before exotic
grasses fully recover (estimate \~ 3 yrs). Koa (*Acacia koa*), a species
uncommon in dry \`ohi\`a woodlands, was included as a restoration
species because of its prolific ability to regenerate from root suckers
in response to disturbance, and its natural occurrence in the area prior
to the burn.

The strategy in mesic koa forest was to create a vegetated fuel barrier
that would reduce the likelihood of fire penetrating Kipuka Puaulu
Special Ecological Area (Figure 1). Kipuka Puaulu is a rare mesic
soapberry-koa-\`ohi\`a community that contains a number of endangered
and rare plant species. Surrounding the Kipuka is degraded koa forest
that is vulnerable to wild fire. These are koa forests that have
regenerated in abandoned pastures following the removal of cattle in the
1950\`s. Koa came up vigorously and reformed a forest canopy, but very
little regeneration of the subcanopy and understory vegetation occurred.
The result was an over-simplified koa community composed of koa and
alien grasses (*Ehrharta stipoides, Pennisetum clandestinum)* that was
more vulnerable to wild fire. In the Broomsedge Burn, fire carried by
meadow ricegrass (*Ehrharta stipoides*) burned 85 ac of koa forest and
came within 50 m of Kipuka Puaulu Special Ecological Area before
changing weather conditions and control lines constructed by fire
fighters stopped the fire. Restoration efforts were focused on restoring
the native understory that existed prior to ungulates in degraded koa
forest that lie immediately adjacent to Kipuka Puaulu. Re-establishing
native understory plants would create a shadier, moister environment
that would suppress alien grasses and possibly reduce the risk of fire
being carried in this environment and penetrating Kipuka Puaulu. The koa
canopy that was damaged by fire is expected to recovery naturally
through vigorous production of root suckers (Parman 1976, Hauss
unpubl.). Seeds and cutting of nineteen native plant species were
collected and individuals propagated in park greenhouses and
subsequently outplanted beneath the koa (Table 1).

The same strategy, to increase fire resistance by establishing a thick
understory beneath a strip of koa forest, was used to reduce the
likelihood of fire carrying between the Park and private landowners in
the nearby Volcano Golf Course Subdivision. This is an area where young
koa stands were beginning to naturally establish in \`ohi\`a woodlands
(Figure 1). Eleven native species were propagated and subsequently
outplanted beneath a 400 m strip of naturally recovering koa (Table 1).
A subset of species was also established by artificial seeding of the
area. Koa was outplanted in sections of the strip where the density of
trees was sparse in order to establish a continous strip of koa forest.

In addition to native plant introductions, ecologically disruptive alien
plant species were prevented from establishing in the burn. Faya tree
(*Myrica faya*), Himalayan blackberry (*Rubus argutus*), Himalayan
raspberry (*Rubus ellipticus*) and strawberry guava *(Psidium
cattleianum*) are invasive weeds that have the potential to form dense
stands or thickets that displace native plant communities and disrupt
ecosystem processes (Smith 1985). Faya tree is a nitrogen-fixing tree
that forms dense monotypic stands that excludes all native vegetation,
and increases nitrogen inputs upto four-fold in invaded areas (Vitousek
and Walker 1989). Strawberry guava is considered among the worst weeds
in lowland Hawaiian forest (Smith 1985, Huenneke and Vitousek 1990).
Individuals establish across a broad range of light environments (Loh
2004), and form dense monospecific stands that preclude all other
vegetation. Himalayan raspberry and blackberry are major pests that form
large persistent thickets or mats in seasonally dry and mesic forest
(Smith 1985). These species are present in low numbers in unmanaged
areas near the burn (Benitez unpubl.), and may severely limit native
plant restoration if allowed to establish in the burn. Between 2001 to
2003, work crews searched and chemically or manually removed these
species in the burn.

Vegetation monitoring to evaluate recovery of the vegetation and the
efficacy of the restoration efforts was conducted between 8/01 and 4/04.
Included were measurements of native outplant survivorship, recruitment
from seed additions, and natural recovery of the vegetation community
following wildfire.

# 

# **Methods**

**[Native Plant Restoration]{.underline}**

# \`ohi\`a woodland 

In \`ohi\`a woodlands, restoration of native plants was concentrated in
693 plots that were established along 52 transects that spanned the burn
(Figure 1). Plot density was \~ 4 plots/hectare). Transects started at
the Mauna Loa Strip Road and extended perpendicular from the road in
both directions (40, 220 degrees). Transects were labeled A through Z
east (40 degree bearing) or west (220 degree bearing). Circular plots
(15 m radius) were established at 50 m intervals along each transect.

Addition of 2,000-3,000 seeds/plot of \`a\`ali\`i (a shrub) and 400-600
seeds/plot of mamane (a tree) were conducted in all of the plots. Fifty
to a hundred seeds of ko\`o ko\`o lau (*Bidens hawaiiensis*) (a shrub)
and 200-300 seeds of koa (tree) were added to a subset of plots. Seeds
were scattered and mixed in the soil layer ([\<]{.underline}1 cm depth)
by lightly turning over the soil with a rake or potato digger. The first
round of seeding into plots occurred between 8/00 to 2/01. A second
round of seeding took place in 2002-2003. Recruitment from seed addition
was monitored by counting the number of seedlings in 40 plots. Seedlings
were categorized by height (\<10, 10-50, 50-100, \>100 cm height) and a
subset of individuals (\>10 cm height) was tagged to look at one year
survivorship. Twenty monitoring plots were also established away from
seeded plots to serve as unseeded control plots. Monitoring of seedling
recruitment took place in 8/01 and 6/03.

Outplanting of 15 native plants species was conducted in 450 plots
(Table 1). Number of outplants varied between 4 to 57 indiv/plot.
Average plot density was 23 indiv/plot. Outplants included 13
fire-tolerant plant species. A limited number of \`ohi\`a and pukeawe
were outplanted in the burn. These species are considered relatively
fire-intolerant, but were planted because they were the major components
in the pre-burn community. Fire tolerant \`a\`ali\`i was not outplanted
because recruitment from artificial seeding into plots was expected to
be high based on previous studies (Loh *et al.* unpubl.). Outplanting
first began in December 2000 and continued to July 2003 as individuals
propagated in the nursery matured and became available for outplanting
in the burn. There were a total of thirty outplanting sessions.
Survivorship of outplanted individuals, their vigor, and reproductive
status, was monitored in 60 plots in 3/02 (halfway through the
outplanting sessions) and in 4/04 (8 mo. after the last round of
outplanting).

# Koa-\`ohi\`a mesic forest

Restoration of native understory plants was concentrated in a 50 m x 400
m strip of burned koa forest that lay adjacent to Kipuka Puaulu SEA
(Figure 1). The planting area was subdivided into 75 plots (approx 10-15
m radius) within which planting and seeding was concentrated. Eighteen
native species were outplanted between 8/00 and 5/03 (Table 1). Total
plant density in the 50 x 400 m strip was 2,520 indiv/ha. Plots were
seeded with \`a\`ali\`i (500-1500 seeds/plot), mamane (200-600
seeds/plot), and manele (*Sapindus saponaria*) (50-150 seeds/plot).
Herbicide control of meadowrice grass with 1% Roundup in water was
performed quarterly inorder to minimize competition from alien grasses
while outplants established. Outplant survivorship of nine species was
monitored in 3/02 or midway through the project. Monitoring of seedling
recruitment from seed addition was not conducted.

# Young koa stands

Establishment of koa and native understory plants was concentrated in a
50 m x 400 m burned strip that lay \~100m west and parallel to the Park
boundary adjacent to the Volcano Golf Course Subdivision. The planting
area was subdivided into 60 plots (approx 15 m radius) within which
planting and seeding was concentrated. Natural recovery of fire-damaged
koa stands was augmented with outplants of koa and 10 other native
species between 3/02 to 2/22/03 (1,327 indiv/ha). Seed addition of koa
(250-900 seeds/plot), mamane (1,400-2,200 seeds/plot) and \`a\`ali\`i
(4,000-10,000 seeds/plot) was conducted in all the plots. No outplant
survivorship or seedling recruitment was monitored in this site.

[Seed collection, seed preparation, seed storage]{.underline}

Plant material for propagation and seeding in the burn was collected
from individuals and populations located closest to the burn. Material
was collected from as many individuals as possible in order to maximize
genetic diversity. For common species, material was collected from \>100
individuals. For less common species, material was collected from at
least 25 individuals. Fewer than 10 individuals were used as source
material for locally rare native tree species, alani (*Meliocope
radiata*), and kolea (*Myrsine lessertiana*) that were outplanted in
mesic koa forest.

Fruits were generally pulped and removed from the seed before
broadcasting into the burn or for plant propagation. Seeds of
\`a\`ali\`i remained in their capsules for broadcasting in the burn.
Seeds were stored in refrigerators with the exception of the legumes,
which were stored at room temperature before they were husked, and
\`a\`ali\`i.

Plant propagation was conducted in temporary park greenhouses that were
constructed for the project. A 100 x 24 ft hoop house, and two 20 x 20
ft nurseries were constructed by March 2001. Twenty-four 4x12 ft benches
were built and, combined with 30 benches provided by the park, were
devoted to propagation of native plants for outplanting into the burn.
Many of the species had not been propagated or outplanted in the park in
recent years (e.g. *Santalum paniculatum, Charpenteria obovata, Melicope
radiata*). Plant propagation techniques had to be developed or refined
for the rehabilitation project. Propagation techniques, and sanitation
protocols developed for the project are currently being summarized in a
separate technical report (Mcdaniel pers. comm.).

**[Alien Plant Control]{.underline}**

Work crews conducted systematic sweeps on foot and removed alien woody
species, Himalayan blackberry (*Rubus argutus*), Himalayan raspberry
(*Rubus ellipticus)*, strawberry guava (*Psidium cattleianum*) and faya
tree (*Myrica faya*) from the entire burn. Individuals were either
manually uprooted or stems were cut and Garlon 3a (10% in water) applied
to stumps. Treatment was conducted annually between 2001-2003.

**[Monitoring Natural Recovery in the Burn]{.underline}**

Additional monitoring to evaluate community response to fire and
rehabilitation activities was conducted in permanent plots. Sixty 30 x
20 m plots were established in the burn, forty inside planting plots and
twenty outside the planting plots to document vegetation changes
following fire and management. Half of the plots were located in an area
that had been twice burned (2xburn), once in 1977 and again in the
Broomsedge Burn. The remainder was established in an area that had only
burned once in the Broomsedge Burn (1xburn). Ten additional 30 x 20 m
control plots were established in adjacent unburned \`ohi\`a woodlands.
Inside the plots, vegetation cover, native seedling recruitment and tree
survivorship were recorded, following modified protocols described in
the Fire Monitoring Handbook (NPS 1992). Modifications to the FMH
protocols included 1) reduction of plot size (20 x 30 m), and 2) trees
categorized by basal diameter rather than DBH. Monitoring was conducted
in summer 2001, one year after the fire, and at the end of the project
in 2003. Also, recovery of native \`ohi\`a (n=206) and koa (n = 97)
individuals were monitored along 6 transects that spanned the burn. Fire
severity (char height, scorch height, percent canopy scorch) on
individuals was quantified within the first month following fire, and
individual survivorship (as evidenced by regrowth at the base or along
the trunk and branches) was monitored one year later.

**[Data Analysis]{.underline}**

Survivorship of outplanted species was summarized as the percent of live
individuals among the total number of individuals that were monitored
across all sample plots within a community type (\`ohi\`a woodland, koa
mesic forest).

Seedling recruitment from seed additions into plots was summarized as
the average number of individuals (by height class, or across all height
classes) per plot present in seeded and unseeded plots. Extremely low
recruitment in unseeded plots prevented statistical comparison between
seeded and unseeded plots. Survivorship of tagged seedlings was
summarized as the percent of live individuals among the total number of
individuals that were monitored across all sample plots.

To evaluate natural recovery of plants in the burn, a one-way ANOVA
(SYSTAT ver. 9) was used to compare plant abundances among the 1xburn,
2xburn and unburn plots. For cover and density data, species were
grouped and analyzed by life form category (exotic herb, exotic grass,
exotic woody, native herb, native woody, native grass). Count data were
log-transformed and cover data were arcsine transformed. Tukey multiple
comparison tests were performed to identify significant treatment
responses across sites.

Survivorship of \`ohi\`a, and koa was summarized as the percent of live
individuals (as evidenced by basal or epicormic live foliage) among the
total number of individuals that were monitored along transects.
Average, minimum and maximum char height, scorch height and percentage
of crown scorch of individuals were summarized for each species.

**[Results]{.underline}**

**[Native Plant Restoration Treatment]{.underline}**

Approximately 3000 worker days (1239 volunteer days) were spent on
restoration efforts in the burn. The majority of the time was devoted to
collecting seeds, propagating individuals, sowing seeds and outplanting
in the burn. Eight hundred twenty-eight planting plots were established,
75 in koa-\`ohi\`a mesic forest, 693 in \`ohi\`a woodland, and 60 in
young koa stands. Nearly nineteen thousand (18,798) individuals of 30
species were outplanted and 2,735,100 seeds of five species were sown in
the burn.

Survivorship was high among outplants despite no supplemental watering
in the field. Average survivorship across all 16 species planted in
fire-damaged \`ohi\`a woodlands was 81% (Table 3). Survivorship among
species ranged from a high of 96% for koa trees, to 60-85% for most
other species and a low of 32% for \`emoloa grass (*Eragrostis
variabilis*) and 33% for pua kala or Hawaiian poppy (*Argemone
glaucum*). The low survivorship of the latter two species is not
unexpected since the poppy is an annual species that dies after seed
production, and the emoloa was difficult to relocate amid the tall alien
grasses (outplants were not flagged). First year outplant survivorship
for nine species monitored in mesic koa forest was much higher (\>90%)
(data not shown). However, monitoring was done midway through the
outplanting program and numbers of planted individuals were low for some
species (e.g. \< 10 indiv). More monitoring is needed to reliably
determine outplant success for all species planted in the koa mesic
forest. No monitoring was conducted for individuals outplanted in young
koa stands. This environment is very similar to \`ohi\`a woodlands, and
outplant survivorship is expected to be similar to survivorship in plots
located in fire-affected \`ohi\`a woodlands.

  ------------------------------------------------------- ---------------
  ![](media/image2.png){width="4.670138888888889in"       Native
  height="3.5027777777777778in"}                          understory
                                                          outplanted
                                                          beneath mesic
                                                          koa forest May
                                                          2002. All
                                                          plants are
                                                          outplanted
                                                          except for big
                                                          trees. Outplant
                                                          survivorship
                                                          was \>90% for
                                                          the nine
                                                          species
                                                          monitored
                                                          midway through
                                                          the outplanting
                                                          project.

  ------------------------------------------------------- ---------------

There was significant seedling recruitment from seed additions into
plots for koa, mamane, \`a\`ali\`i, and ko\`o ko\`o lau located in
fire-affected \`ohi\`a woodlands (Figure 2). Seedling survivorship of
tagged individuals \>10 cm height between 8/01 to 6/03 was 35% for
mamane, 69% for koa, 98% for \`a\`ali\`i, and 100% for ko\`o ko\`o lau.
Recruitment from seed addition into plots was observed but not
quantified for manele (*Sapindus saponaria*), mamane, and \`a\`ali\`i in
mesic koa forest, and for mamane and \`a\`ali\`i in young koa stands.

  ---------------------------------------------------- -----------------------------------------------------
  ![](media/image3.jpeg){width="2.577777777777778in"   ![](media/image4.jpeg){width="2.8368055555555554in"
  height="2.129861111111111in"}                        height="2.1194444444444445in"}

  Seedling recruitment of \`a\`ali\`i from seeds       Seedling recruitment of mamane and manele from seeds
  placed in plots in fire-damaged \`ohi\`a woodland.   placed in plots in fire-damaged mesic koa forest.
  ---------------------------------------------------- -----------------------------------------------------

Individuals of ten outplanted species and \`a\`ali\`i were
reproductively mature (seed production or root suckers) at the time of
the last sampling (4/04) (Table 3). These included 4 tree species
(mamane, mamaki, naio, koa by root suckers), 3 shrubs (\`a\`ali\`i, nae
nae, ko\`o ko\`o lau), a lily (\`uki\`uki), pua kala or the Hawaiian
poppy, and 2 grasses (*Eragrostis variabilis*, *Deschampsia nubigena*).
Seed production was widespread among outplanted ko\`o ko\`o lau and
grasses, but less common for other outplanted species. Outplanted
individuals of naio (*Myoporum sandwicensis*) and mamaki (*Pipturus
albidus*), small trees, were producing fruit in mesic koa plots but not
in dry \`ohi\`a woodland plots. Future monitoring will determine whether
seed production will lead to successful seedling establishment in the
plots.

**[Alien Plant Treatment]{.underline}**

Ten percent (311 worker days) of work time devoted on the projects, was
spent searching and removing disruptive alien species that threatened
native plant recovery in the burn. Over seven thousand (7,409)
individuals of Himalayan blackberry (*Rubus argutus*), Himalayan
raspberry (*Rubus ellipticus*), strawberry guava (*Psidium cattleianum*)
and faya tree (*Myrica faya*) were found and removed between Summer 2001
to Summer 2003. Spot application of herbicide on meadowrice grass
(*Erharta stipoides*) was used to reduce competition to native outplants
in mesic koa forest. Work crews consisted of personnel form the Division
of Resources Management, contract employees through cooperative
agreements, Youth Conservation Corps, and volunteer biologists.

**[Plant community Response to fire]{.underline}**

Three years after fire, exotic grasses had re-established rapidly in the
1x and 2x burn areas (Figure 3). Percent cover of exotic grasses was
within two-thirds of adjacent unburn areas. Both species richness and
cover abundance of exotic herbaceous species were much greater in the
burn than in the adjacent unburn. In contrast native woody and
herbaceous species had significantly less plant cover in the burn
relative to adjacent unburn areas. Density of mature native shrubs,
pukeawe and \`a\`ali\`i, was significantly higher in the unburn (8
indiv/plot for \`a\`ali\`i, 148 indiv/plot for pukeawe) than in the 1x
burn (\<1indiv/plot for \`a\`ali\`i and pukeawe), and 2x burn (\<1
indiv/plot for a\`ali\`i, and 2 indiv/plot for pukeawe). Few
fire-affected \`a\`ali\'i and pukeawe survived the burn by resprouting
at the base of fire damaged individuals. Average seedling recruitment
(\<10 cm height) of \`a\`ali\`i was 20-fold greater in the 1xburn (19
indiv/plot) and 2xburn (21 indiv/plot) than in the unburn (1.5
indiv/plot). There was no significant difference in small seedling
recruitment (12-65 indiv/plot) of pukeawe between the 1x, 2x burn and
unburn. Survival by resprouting was common for ohelo (*Vaccinium
reticulatum*) in the 1x burn (62 indiv/plot) and 2x burn (9 indiv/plot).

Among the 97 fire-damaged koa trees that were monitored, greater than
95% were top killed. Char height ranged between 0.7 to 3.1 m height
(average char height = 1.8 m), scorch height ranged between 2.6 to 8.0 m
height (average scorch height = 5.2 m), percent crown scorch was between
66 to 100% (average % crown scorch = 90%). One year after fire, 55% of
individuals had resprouted (92% basal, 8% epicormic). Among fire-damaged
\`ohi\`a (n= 206), char height ranged between 0.4 to 2.8 m height
(average char height = 2.3 m), scorch height ranged between 2.0 to 5.1 m
height (average scorch height = 4.1 m), percent crown scorch was between
23 to 100% (average % crown scorch = 87%). One year after fire, 68% of
individuals had resprouted (resprouting was 86% basal and 26% epicormic
among live individuals).

**[Discussion]{.underline}**

Rehabilitation of the Broomsedge Burn was the first attempt by park
managers to restore fire-affected dry \`ohi\`a woodland communities at
Hawai\`i Volcanoes National Park. Field and laboratory experiments
conducted between1993-2000 had identified fire-tolerant native plant
species for restoration into burn sites (Loh in prep.). Techniques for
getting species established through artificial seed banks had also been
tested. The Broomsedge Burn provided managers the opportunity to apply
the knowledge gained in past experiments to restoration of a large burn.

**[Establishment of native plants by outplanting and
seeding]{.underline}**

Native plant establishment through outplanting and seeding appeared
successful based on early monitoring results. Outplant survivorship was
\>80% in fire-affected dry \`ohi\`a woodlands and \>90% in koa mesic
forest. This is relatively high survivorship when compared to
survivorship or native species planted in other parts of the park, many
of which required additional watering in the field (Belfield pers.
comm.). High survivorship may be partially due to more favorable
moisture conditions. The burn is located on the upper elevational extent
of the dry \`ohi\`a woodlands that transitions into mesic forest.
Outplant success is expected to be considerably lower in restoration
projects conducted in drier parts of the \`ohi\`a woodlands. Also, the
time that elapsed between when individuals were first outplanted and
last monitored varied between 8 mo and 3 years. Consequently, some
mortality of recently outplanted individuals may occur in the future.

Successful seedling recruitment from artificial seeding into the burn
was evident for the five species (mamane, \`a\`ali\`i, koa, ko\`o ko\`o
lau, manele) where seeds were placed in plots. One year survivorship of
tagged individuals (mamane, \`a\`ali\`i, koa, ko\`o ko\`o lau) was
35-100%, and suggests that some seedlings will continue to grow to reach
reproductive maturity. Seedling survivorship in the burn was relatively
high compared to research sites in other parts of the dry \`ohi\`a
woodlands (Ainsworth unpubl., Vayadati pers. comm.), and maybe partially
due to more favorable moisture conditions in the burn. There were other
species (e.g. \`ili\`ahi, na\`e na\`e) that might have successfully
established from artificial seeding, based on observations in
experimental burns and life history characteristics, but the amount of
seeds available was insufficient for distributing across plots.

By 2004, individuals of ten outplanted species and \`a\`ali\`i had grown
to reproductive maturity in the burn. Nine species, including
\`a\`ali\`i, showed either fruit production or regeneration by root
suckers (koa) in \`ohi\`a woodland plots. Two additional tree species
(mamaki, naio) were producing fruit in mesic koa forest plots. These are
positive steps toward the long-term establishment of native species in
the burn. Particularly for \`ohi\`a woodland, where a grass-fire cycle
has established with the invasion of fire-adapted grasses, establishment
of a soil seed bank of fire-tolerant species before another wild fire
occurs is required to ensure the long-term persistence of re-introduced
species. The assumption, based on observations in previous wildfire and
research burns, is that future fires may top-kill individuals, but these
fire-tolerant species will survive and proliferate through vegetative
regrowth and seedling recruitment from the soil seed bank in response to
fire.

**[Prevention of alien woody species establishment]{.underline}**

Four of the most ecologically disruptive alien species were prevented
from establishing in the burn. Over 7,000 individuals of Himalayan
raspberry, Himalayan blackberry, faya tree, and strawberry guava were
removed between 2001-2003. The intent of the search and control effort
was to prevent these species from becoming established during the
interim that followed the burn, when the area is largely unoccupied by
plants and most vulnerable to invasion by alien species. By 2003, plant
cover in the burn had not yet recovered to adjacent unburn levels.
Future monitoring will determine whether these four disruptive alien
woody species will continue to invade the burn, and whether search and
control efforts need to be continued.

**[Natural recovery of preburn community after fire]{.underline}**

Natural recovery of \`ohi\`a was relatively high compared to documented
recovery in other fire-affected \`ohi\`a woodland sites in the park
(Tunison *et al.* 1995). Individuals were top-killed, but at least
2/3rds of individuals were able to regenerate from resprouting at the
base of trees. \`Ohi\`a survival through resprouting after fire varied
considerably between 0% to 49% in other areas of the park and survival
appeared partially dependent on burn severity and tree size (Tunison *et
al.* 1995). Occasional seedlings were observed in the burn, but numbers
were insufficient to detect in plots, and it is doubtful that seedlings
will contribute much to the future recovery of \`ohi\`a stands. This may
lead to continued stand reduction with recurrent fire in the future.

Pukeawe, the dominant native shrub in the preburn community, was also
heavily impacted by fire. Almost all individuals damaged by fire in
plots were top-killed, and no vegetative resprouting was observed.
Future recovery will depend on recruitment from the existing seed bank.
Seedling occurrence was highly variable in burn plots. Seedlings grow
extremely slow and have difficulty surviving in competition with exotic
grasses after fire (Hughes and Vitousek 1993). Future monitoring will
determine the extent to which individuals survive and grow in the
presence of the exotic grasses that are recovering rapidly in the burn.

\`A\`ali\`i and koa are two fire-tolerant species that were present in
the preburn communities. Most \'a\'ali\'i individuals were top killed
and very little vegetative resprouting at the base of stems was
observed. Seedlings were evident and in greater abundance in burn plots
than in adjacent unburn plots. A\`ali\`i shrub densities and cover
increase, primarily through seedling recruitment, in response to fire
(D\`antonio *et al.* 2000, Tunison *et al.* 1995). Fifty-five percent of
koa resprouted following fire-damage in mesic koa forest. Koa is a
disturbance adapted tree that regenerates through vigorous seedling
recruitment and root suckers (Vogl 1969, Spatz 1973). Prolific
recruitment from the natural seed bank and root suckers was evident but
not quantified in this burn.

**[Conclusions]{.underline}**

Rehabilitation of native plants in the Broomsedge Burn serves as the
model for restoration in other fire-affected dry \`ohi\`a woodlands in
the Park. Over fifteen thousand acres, or two-thirds of dry\`ohi\`a
woodland have been affected by wildfire in the older section of Hawai\`i
Volcanoes National Park. The remaining unburn areas have been invaded by
alien grasses and have the potential to burn which would result in
further conversion of \`ohi\`a woodland to alien grass savanna. Since
the Broomsedge Burn, three wildfires (Kupukupu (2002), Panau Iki (2003),
Kipuka Pepeiao (2004)) have affected nearly 3,000 acres of dry or
transitionally dry \`ohi\`a woodland. These include previously burned
areas and large areas where fire had not historically been documented
(Tunison unpubl.). Restoration of fire-tolerant native species has begun
in sections of the Kupukupu burn, and plans are being developed to
re-introduce fire-tolerant species in Kipuka Pepeiao.

Based on the results of this project, the following management
recommendations can be made for future restoration of other
fire-affected dry ohia woodlands in HAVO:

1.  Establish seed stockpiles and plant orchards to increase plant
    material available for large-scale restoration. In the Broomsedge
    Burn (1,008 ac), low supplies of plant material and seeds limited
    the pace of plant production and, in some instances, the number of
    individuals of a species established in the burn. A lot of time
    (estimated 40% of volunteer worker days) was devoted to searching
    and collecting plant material for plant propagation and seeding.
    Collecting large quantities of seed and stockpiling them will enable
    managers to form a rapid response to future restoration emergencies.
    For species with seeds that do not remain viable in storage over
    years (Yoshinaga 2002), or whose seeds are extremely scarce, plant
    orchards should be established. Cultivation of stock material would
    be in outdoor nurseries or in natural areas, and would provide a
    steady supply of plant material for future propagation and
    restoration. Orchards would also protect genetic integrity of
    species, by preserving plant material collected from source material
    that may be otherwise inaccessible or vulnerable to stochastic
    events.

2.  Continue refining and developing new techniques for plant
    propagation to make more effective use of limited plant material and
    maximize the pace and output of plant production. For the Broomsedge
    Burn, many of the species had not been propagated or outplanted in
    the park in recent years (e.g. *Santalum paniculatum, Charpenteria
    obovata, Melicope radiata*). Consequently plant propagation
    techniques had to be developed or refined for the rehabilitation
    project. Plant production increased overtime as propagators
    developed new techniques for cultivating plants that used limited
    seed supplies more effectively (e.g. germination rates were
    increased), employed alternatives techniques than seeds (e.g.
    cuttings), and increased growth and survivorship in the nursery.
    Only a subset of fire-tolerant species was used in the Broomsedge
    Burn. These were species that had previously existed in the
    surrounding areas but had been previously removed by feral goats
    (goats are now excluded from the park). There are other
    fire-tolerant species that are appropriate for reintroduction in
    lower elevation \`ohi\`a woodlands (1,500-3000 ft elevation) and new
    fire-tolerant species are being identified in ongoing field studies.
    Techniques for their cultivation will need to be developed or
    refined for future restoration in burns.

3.  Continue to monitor vegetation changes in the Broomsedge Burn and in
    other related restoration experiments and projects. Among the
    biggest uncertainties for managers was determining the appropriate
    number of individuals needed to establish species in the burn. For
    the Broomsedge burn, the restoration strategy was to create small
    fire-tolerant native plant associations scattered across the burn.
    The assumption was that individuals would mature, reproduce, and
    eventually establish a soil seed bank for future proliferation with
    the next fire event. This jumpstart approach toward the development
    of an alternative fire-tolerant native plant community was perceived
    as the most feasible strategy for rehabilitating large expanses of
    dry \`ohi\`a woodlands. The Broomsedge Burn served as a test for
    this model. Initial establishment of species was highly successful.
    However, what remains unknown are the number of species individuals,
    number and placement of plots, and time-required between fire
    intervals needed to ensure the future establishment of a
    fire-tolerant community. Outcomes will vary depending on site
    conditions, and fire frequency. Also, fire-tolerance was identified
    through testing seed response to small research burns and in
    laboratory experiments, and from observations (informal and
    quantitative measurements) of plant recovery from wildfires in and
    out of the park. The real test of fire-tolerance for these
    artificially created communities will be with the next wildfire.
    Consequently, long term monitoring in multiple restoration projects
    is needed to help managers determine the success of their treatments
    and effectively plan for future restoration projects.

> Long-term monitoring is also needed to evaluate the effectiveness of
> the two vegetated fuel breaks that were established in the Broomsedge
> Burn. The concept of building dense vegetation to slow or stop fire
> spread is new to HAVO managers. Microclimate changes that enhance fire
> potential have been associated with the conversion of \`ohi\`a
> woodlands to alien grass savannas (Friefelder *et al.* 1998).
> Currently, individuals planted in the vegetated strips are too small
> and immature to change microclimate conditions and reduce fuel loads
> sufficiently to slow fire spread. Monitoring will determine whether
> the vegetation increases and microclimate changes occur in the future.
> The ability of the mature fuel breaks to resist fire remains to be
> tested.
>
> Finally monitoring natural recovery in burns should continue. The
> relatively high survivorship of \`ohi\`a in the Broomsedge Burn
> compared to previous studies underscores the need to understand the
> role site conditions, life history, fuel conditions, and burn severity
> have in determining successional outcomes. By understanding how these
> factors influence native species recovery, managers will be able to
> better predict potential recovery following fire and prioritize sites
> for management.

**[Literature Cited]{.underline}**

D\`Antonio, C.M. and P.M. Vitousek. 1992. Biological invasions, the
grass-fire cycle and global change. Ann. Rev. Ecol. Sys. 23:63-87.

D\`Antonio, C.M., F.R. Hughes, M. Mack, D. Hitchcock, and P.M. Vitousek.
1998. The response of native species to removal of invasive exotic
grasses in a seasonally dry Hawaiian woodland. Journal of Vegetation
Science 9:699-712.

D\`Antonio, C.M., J. T. Tunison, and R.K. Loh. 2000. Variations in
impact of exotic grasses and fire on native plant commmunities in
Hawaii. Journal of Australian Ecology 25:507-522.

Freifelder, R., P. M. Vitousek, C.M. D'Antonio. 1998. Microclimate
effects of fire-induced forest/grassland conversion in a seasonally dry
Hawaiian woodlands. Biotropica 30:286-297.

Higashino, P., and L. Cuddihy. 1988. Checklist of vascular plants,
Hawaii Volcanoes National Park. Cooperative Park Studies Unit Technical
Report No. 64. University of Hawaii at Manoa, Honolulu, Hawaii.

Huenneke, L. F., and P. M. Vitousek. 1990. Seedling and clonal
recruitment of the invasive tree *Psidium cattleianun*: implications for
management of native Hawaiian forests. Biological Conservation
53:199-211.

Hughes, F, P.M. Vitousek, and T. Tunison. 1991. Alien grass invasion and
fire in the seasonal submontane zone of Hawai\`i. Ecology 72(2):743-746.

Hughes, R.F. and P.M. Vitousek. 1993. Barriers to shrub reestablishment
following fire in the seasonal submontane zone of Hawai\`i. Oecologia
93:557-563.

Loh, R. K. 2004. Early plant establishment following experimental
removal of invasive *Morella faya* (Wilbur) Ait. stands in a Hawaiian
forest. Dissertation, University of Hawaii at Manoa, Honolulu, Hawaii.

Loh, R. K., A. Ainsworth, T. Tunison, C. M. D\`Antonio. In prep. Testing
native species response to prescribed fire in Hawaii Volcanoes National
Park.

National Park Service. 1992. Western Region Fire Monitoring Handbook. US
Department of

Interior.

Parman, T.R. 1976. The effects of fire on a Hawaiian montane ecossytem.
In Proc. Of the First Conference in Natural Sciences. Hawaii Volcanoes
National Park. C.W. Smith (ed). University of Hawaii, Honolulu.

Smith, C.W. 1985. Impact of alien plants on Hawaii s native biota*. In*
Hawaii\`s Terrestrial Ecolsystems: Preservation and Management. C.P.
Stone and J.M. Scott, eds. University of Hawaii Press. 584 pp.

Spatz. 1973. S ome findings on vegetative and sexual reproduction of
koa. Island Ecosystem IRP U.S. IBP Technical Report No. 4. University of
Hawaii at Manoa, Honolulu, Hawaii.

Tunison, J.T., R.K. Loh and J.A.K. Leialoha. 1995. Fire effects in the
submontane seasonal zone, Hawai\`i Volcanoes National Park. Technical
Report 97. Cooperative Parks Resources Studies Unit. University of
Hawai\`i, Honolulu.

Yoshinaga, A. Y. 2002. Seed storage practices for native Hawaiian
Plants. http://www2. Hawaii.edu/scb/seed/seedmanual.html.

Vitousek, P. M., and L. R. Walker. 1989. Biological invasion by *Myrica
faya* in Hawaii: Plant demography, nitrogen fixation, and ecosystem
effects. Ecological Monographs 59(3):247-265.

Vogl, R.J. 1969. The role of fire in the evolution of the Hawaiian flora
and vegetation. pp 5-60 [In]{.underline} Proceedings Tall Timbers
FireEcology Conference (9).

Table 1. Natives species for introduction into burned communities. X
denotes establishment by outplanting, x denotes establishment by
artificial seeding, \* denotes fire-tolerant species.

  ----------------- ---------------------- ----------- ----------- -----------
  Species                                  Pre-burn                
                                           Community               

  Common Name       Scientific Name        Ohi\`a      Young Koa   Mesic Koa
                                           Woodlands   Stands      Forest

                                                                   

  **Overstory                                                      
  trees**                                                          

  Manele            *Sapindus saponaria*                           Xx

  Koa\*             *Acacia koa*           Xx          Xx          

  \`Öhi\`a          *Metrosideros          x           x           x
                    polymorpha*                                    

                                                                   

  **Small trees**                                                  

  Alani             *Melicope hawaiiensis*                         x

  Hoawa             *Pittosporum hosmeri*                          x

  Hoawa             *Pittosporum           x                       
                    terminoides*                                   

  \`Iliahi\*        *Santalum paniculatum* x           x           x

  Kölea             *Myrsine lessertiana*                          x

  Köpiko            *Psychotria                                    x
                    hawaiiensis*                                   

  Mämaki            *Pipturus albidus*                             x

  Mämane\*          *Sophora chrysophylla* Xx          Xx          Xx

  Naio\*            *Myoporum sandwicense* x           x           x

  Olopua            *Nestegis                                      x
                    sandwicensis*                                  

  Papala            *Charpenteria obovata*                         x

  Päpala këpau      *Pisonia brunoniana*                           x

  Pilo              *Corposma rhyncocarpa*                         x

                                                                   

  **Shrubs**                                                       

  \`A\`ali\`i\*     *Dodonaea viscosa*     X           X           X

  Akala             *Rubus hawaiiensis*                            x

  Ko\`oko\`olau\*   *Bidens hawaiiensis*   Xx                      

  Maile             *Alyxia olivaeformis*                          x

  Mä\`ohi\`ohi      *Stenogyne rugosa*                             x

  Na\`ena\`e\*      *Dubautia ciloata*     x           x           

  Naupaka\*         *Scaevola kilaueae*    x                       

  Öhelo\*           *Vaccinium                         x           
                    reticulatum*                                   

  Pükiawe           *Styphelia             x           x           
                    tameiameiae*                                   

  Ülei\*            *Osteomeles            x           x           
                    anthyllidifolia*                               

                                                                   

  **Herbs, ferns,                                                  
  and sedges**                                                     

  Palapalai         *Microlepia strigosa*                          x

  Pua kala\*        *Argemone glaucum*     x                       

  \`Uki\`uki\*      *Dianella sandwicense* x                       

                                                                   

  **Grasses**                                                      

  \`Emoloa\*        *Eragrostis            x           x           
                    variabilis*                                    

  *Deschampsia\**   *Deschampsia           x           x           
                    australis*                                     
  ----------------- ---------------------- ----------- ----------- -----------

Table 2. Number of outplants and seeds added to the burn by species.

  ---------------- --------------------------- ------------- -------------
  Common Name      Scientific Name             Outplanted    Number of
                                               individuals   seeds added
                                                             to burn

                                                             

  **Overstory                                                
  trees**                                                    

  Manele           *Sapindus saponaria*        691           5,250

  Koa              *Acacia koa*                1,794         67,650

  \`Öhi\`a         *Metrosideros polymorpha*   320           

                                                             

  **Small trees**                                            

  Alani            *Melicope hawaiiensis*      24            

  Hoawa            *Pittosporum hosmeri*       75            

  Hoawa            *Pittosporum terminoides*   16            

  \`Iliahi         *Santalum paniculatum*      234           

  Kölea            *Myrsine lessertiana*       32            

  Köpiko           *Psychotria hawaiiensis*    58            

  Mämaki           *Pipturus albidus*          946           

  Mämane           *Sophora chrysophylla*      3,682         455,850

  Naio             *Myoporum sandwicense*      798           

  Olopua           *Nestegis sandwicensis*     10            

  Papala           *Charpenteria obovata*      75            

  Päpala këpau     *Pisonia brunoniana*        254           

  Pilo             *Corposma rhyncocarpa*      1,801         

                                                             

  **Shrubs**                                                 

  \`A\`ali\`i      *Dodonaea viscosa*                        2,197,500

  Akala            *Rubus hawaiiensis*         135           

  Ko\`oko\`olau    *Bidens hawaiiensis*        514           8,850

  Maile            *Alyxia olivaeformis*       282           

  Mä\`ohi\`ohi     *Stenogyne rugosa*          247           

  Na\`ena\`e       *Dubautia ciloata*          598           

  Naupaka          *Scaevola kilaueae*         408           

  Öhelo            *Vaccinium reticulatum*     46            

  Pükiawe          *Styphelia tameiameiae*     428           

  Ülei             *Osteomeles                 1,507         
                   anthyllidifolia*                          

                                                             

  **Herbs, ferns,                                            
  and sedges**                                               

  Palapalai        *Microlepia strigosa*       127           

  Pua kala         *Argemone glaucum*          77            

  \`Uki\`uki       *Dianella sandwicense*      340           

                                                             

  **Grasses**                                                

  \`Emoloa         *Eragrostis variabilis*     1467          

                   *Deschampsia australis*     1712          
  ---------------- --------------------------- ------------- -------------

Table 3. Outplant survivorship of 16 species planted in fire-damaged
\`ohi\`a woodland, Broomsedge Burn. Survivorship was sampled in 60
planting plots or 13% of plots. N = number of individuals that were
monitored.

+---------------+--------------------------+------+--------+----------+
| Species       | Scientific Name          | n    | %Su    | Fruit    |
|               |                          |      | rvival | produ    |
|               |                          |      |        | ction/or |
|               |                          |      |        | root     |
|               |                          |      |        | suckers  |
+---------------+--------------------------+------+--------+----------+
| [Trees        |                          |      |        |          |
| ]{.underline} |                          |      |        |          |
+---------------+--------------------------+------+--------+----------+
| Hoawa         | *Pittosporum             | 16   | 100    | No       |
|               | terminoides*             |      |        |          |
+---------------+--------------------------+------+--------+----------+
| \`Ili\`ahi    | *Santalum paniculatum*   | 49   | 84     | No       |
+---------------+--------------------------+------+--------+----------+
| Koa           | *Acacia koa*             | 168  | 96     | Yes      |
+---------------+--------------------------+------+--------+----------+
| Mamane        | *Sophora chrysophylla*   | 311  | 69     | Yes      |
+---------------+--------------------------+------+--------+----------+
| Naio          | *Myoporum sandwicense*   | 67   | 78     | Yes\*    |
+---------------+--------------------------+------+--------+----------+
| \`Ohi\`a      | *Metrosideros            | 25   | 100    | No       |
|               | polymorpha*              |      |        |          |
+---------------+--------------------------+------+--------+----------+
|               |                          |      |        |          |
+---------------+--------------------------+------+--------+----------+
| [Shrubs       |                          |      |        |          |
| ]{.underline} |                          |      |        |          |
+---------------+--------------------------+------+--------+----------+
| \`            | *Dodonaea viscosa*       |      |        | Yes      |
| A\`ali\`i\*\* |                          |      |        |          |
+---------------+--------------------------+------+--------+----------+
| Ko\`o ko\`o   | *Bidens hawaiiensis*     | 45   | 82     | Yes      |
| lau           |                          |      |        |          |
+---------------+--------------------------+------+--------+----------+
| Na\`e na\`e   | *Dubautia cilioata*      | 62   | 63     | Yes\*    |
+---------------+--------------------------+------+--------+----------+
| Naupaka       | *Scaevola kilaueae*      | 50   | 84     | No       |
| kilauea       |                          |      |        |          |
+---------------+--------------------------+------+--------+----------+
| Pukeawe       | *Styphelia tameiameiae*  | 46   | 78     | No       |
+---------------+--------------------------+------+--------+----------+
| \`Ulei        | *Osteomeles              | 156  | 97     | No       |
|               | anthyllidifolia*         |      |        |          |
+---------------+--------------------------+------+--------+----------+
|               |                          |      |        |          |
+---------------+--------------------------+------+--------+----------+
| #             |                          |      |        |          |
|  Herbs, ferns |                          |      |        |          |
| , and sedges  |                          |      |        |          |
+---------------+--------------------------+------+--------+----------+
| Pua kala      | *Argemone glaucum*       | 25   | 32     | Yes\*    |
+---------------+--------------------------+------+--------+----------+
| \`Uki uki     | *Dianella sandwicensis*  | 53   | 94     | Yes      |
+---------------+--------------------------+------+--------+----------+
|               |                          |      |        |          |
+---------------+--------------------------+------+--------+----------+
| [Grasses      |                          |      |        |          |
| ]{.underline} |                          |      |        |          |
+---------------+--------------------------+------+--------+----------+
|               | *Deschampsia nubigena*   | 155  | 83     | Yes      |
+---------------+--------------------------+------+--------+----------+
| \`Emoloa      | *Eragrostis variabilis*  | 106  | 33     | Yes      |
+---------------+--------------------------+------+--------+----------+
|               |                          |      |        |          |
+---------------+--------------------------+------+--------+----------+
| Total         | Total                    | 1334 | 81     |          |
+---------------+--------------------------+------+--------+----------+

> \*Fruit production was observed for these species outside the time
> frame of the sampling period or in unsampled plots.
>
> \*\*\`A\`ali\`i was established by artificially seeding plots in the
> burns. Individuals were reproductively mature at the time of the last
> sampling.
>
> [Figure 1. Distribution of planting plots in the different native
> plant communities affected by the Broomsedge Burn]{.underline}
>
> ![](media/image5.jpeg){width="6.0in" height="4.5in"}
>
> [Figure 2. Seedling recruitment (all size classes) in seeded and
> unseeded plots located in fire-affected \`ohi\`a woodlands, Broomsedge
> Burn.]{.underline}
>
> ![](media/image6.jpeg){width="6.0in" height="4.5in"}
>
> Figure 3. Average native and alien plant abundance three years after
> the Broomsedge Burn. Reported are average absolute plant cover and
> standard errors in plots located in the once burn (Broomsedge 2000),
> twice burn (Namakani Paio 1977, Broomsedge Burn 2000), and adjacent
> unburned. Treatments that share the same letter do not differ
> significantly (Tukey [test)]{.underline}

![](media/image7.wmf){width="5.5in" height="3.1041666666666665in"}