The Evergreen State College Institutional Repository

Smoking Grass: Germination Responses of Six Native Poaceae Species to Smoke Water Treatments

Item

Title (dcterms:title)

Eng Smoking Grass: Germination Responses of Six Native Poaceae Species to Smoke Water Treatments

Date (dcterms:date)

2016

Creator (dcterms:creator)

Eng Ely, Conrad

Subject (dcterms:subject)

Eng Environmental Studies

extracted text (extracttext:extracted_text)

Smoking Grass:
Germination responses of six native Poaceae species to smoke water treatments

by
Conrad Ely

A Thesis
Submitted in partial fulfillment
of the requirements for the degree
Master of Environmental Studies
The Evergreen State College
June 2016

©2016 by Conrad Ely. All rights reserved.

This Thesis for the Master of Environmental Studies Degree
by
Conrad Ely

has been approved for
The Evergreen State College
by

________________________
Kevin Francis Ph. D.
Member of the Faculty

________________________
Date

ABSTRACT
Smoking Grass:
Germination responses of six native Poaceae species to smoke water treatments
Conrad Ely
The South Puget Sound prairies are one of the most threatened ecosystems in the United
States due to fragmentation, land use changes, non-native species invasion, conifer
encroachment and climate change. From 2009 through 2015, the Sustainability in Prisons
Project (SPP) has grown plugs for the revegetation of this ecosystem. During that time
they have found a number of species to have particularly low germination rates, including
species from the family Poaceae. Historically, these prairies were burned for thousands of
years by Native Americans to promote the growth of plants used for food, fiber and
medicine. The health of the ecosystem has declined in the last 150 years since European
settlers implemented fire suppression practices. In 2004, two separate research teams
discovered a chemical in smoke, karrikinolide (KAR1) that promotes germination in some
species. From 2004 through 2014, 1,355 species from 120 families have been tested for
their responses to smoke and smoke derived products. Of those, 95 species of Poaceae
have been tested, with 46 species having significant increases in germination. This thesis
examines six native Poaceae species that have had poor germination rates in SPP
nurseries, and their responses to plant-derived smoke water. Using the stratification
protocols of SPP, followed by a five-week germination period, one of our six species (E.
glaucus) was found to have a statistically significant (p< 0.029) increase in germination.
Four of our six species (E. glaucus, E. trachycaulus, D. californica, & B. carinatus) had
an average germination rate above 50% in our control group. These species appear not to
be germination limited. Two of our six species (D. oligosanthes var. scribnerianum & D.
acuminatum var. fasciculatum) had an average germination rate below 30% in our
control group. These species may be germination limited.

Table of Contents
List of Figures.................................................................................................................... v
List of Tables .................................................................................................................... vi
Acknowledgements ......................................................................................................... vii
Introduction ....................................................................................................................... 1
Literature Review ............................................................................................................. 6
Introduction ................................................................................................................................ 6
SPS Prairie Environmental History ......................................................................................... 6
Prescribed Fire ........................................................................................................................... 8
Seed Germination ..................................................................................................................... 10
Fire and Germination .............................................................................................................. 12
Plant-Derived Smoke Water ................................................................................................... 15
Smoke Treatments of Poaceae ................................................................................................ 16
Study Species ............................................................................................................................ 18
Implications .............................................................................................................................. 20

Methods and Materials ................................................................................................... 22
Plant Derived Smoke Water .................................................................................................... 22
Assembling the smoker .......................................................................................................... 22
Operation of the smoker ......................................................................................................... 24
Study Species ............................................................................................................................ 25
Experimental Design ................................................................................................................ 26
Seed Stratification .................................................................................................................. 27
Seed Germination ................................................................................................................... 28
Data Analysis ............................................................................................................................ 29

Results .............................................................................................................................. 30
Germination rates .................................................................................................................... 30
Elymus glaucus ...................................................................................................................... 30
Elymus trachycaulus .............................................................................................................. 31
Dichanthelium oligosanthes var. scribnerianum .................................................................... 32
Danthonia californica ............................................................................................................. 33
Dichanthelium acuminatum var. fasciculatum ....................................................................... 34
Bromus carinatus .................................................................................................................... 34
Germination rates compared with SPP and the literature................................................... 35
Vigor .......................................................................................................................................... 36

Discussion ........................................................................................................................ 38
Plant derived smoke water ...................................................................................................... 38


 

iv
 

Overall germination compared to the literature ................................................................... 38
E. glaucus ............................................................................................................................... 39
D. californica .......................................................................................................................... 39
E. trachycaulus ....................................................................................................................... 40
D. oligosanthes ....................................................................................................................... 41
B. carinatus ............................................................................................................................. 42
D. acuminatum ....................................................................................................................... 43
Controlled versus variable growth environment .................................................................. 44
Seed limitations......................................................................................................................... 45
Germination cues from fire ..................................................................................................... 46
Temporal Conditions ............................................................................................................... 48

Conclusion ....................................................................................................................... 49
Bibliography .................................................................................................................... 52

 


 

v
 

List of Figures
Figure 1.1 – Smoking Apparatus………………………………………………………23
Figure 1.2 – Smoker Parts D-G……………………………………………………......24
Figure 2 – Emergent Radicle………………………………………………………......28
Figure 3.1 – Elymus glaucus……………………………………………………………30
Figure 3.2 – Elymus trachycaulus……………………………………………………...31
Figure 3.3 – Dichanthelium oligosanthes var. scribnerianum……...…………………32
Figure 3.4 – Danthonia californica…………………………………………………….33
Figure 3.5 – Dichanthelium acuminatum var. fasciculatum…………………………..34
Figure 3.6 – Bromus carinatus…………………………………………………………35


 

v
 

List of Tables
Table 1 – Seed Collection Origin………………………………………………………26
Table 2 – Experiment Time Table……………………………………………………..26
Table 3.1 – Elymus glaucus…………………………………………………………….30
Table 3.2 – Elymus trachycaulus…………………………………………………….....31
Table 3.3 – Dichanthelium oligosanthes var. scribnerianum………………………….32
Table 3.4 – Danthonia californica……………………………………………………...33
Table 3.5 – Dichanthelium acuminatum var. fasciculatum…………………...……....34
Table 3.6 – Bromus carinatus…………………………………………………………..35
Table 4 – Germination rates as compared with the literature……………………….36
Table 5 – Time to 50% Germination (t50)…………………………………………….37


 

 


 

vi
 

Acknowledgements

I would like to thank the MES faculty, and specifically Kevin Francis for teaching me
throughout graduate school and the thesis process. The Sustainability in Prisons project
also played a special role in this thesis, and I thank all of my coworkers and crew for their
motivation and involvement. I could not have gotten this far without my peers in the
MES program, and specifically Rebekah Korenowsky, Allie Denzler and Sarah Krock for
their contributions to this thesis. Finally, I could not have made it through these last two
years without the support of my loving parents Kathy and John, my devoted partner
Katie, and my ever-distracting pup Marshawn.


 

vii
 

Introduction
Restoration of the South Puget Sound Prairies is a challenging endeavor. These
grasslands are highly fragmented, existing as small islands amidst a sea of anthropogenic
land use. Geographically separated by roads, farms, neighborhoods, towns and conifer
forests, much of the challenge in restoring this habitat comes from a lack of natural
regeneration of the plant community (Dunwiddie & Bakker, 2011). In order to augment
this ecosystem, restoration organizations plant out native seeds and plugs to bolster the
diversity. However, limited seed banks and low germination rates continue to pose a
problem for restoration ecologists.
Ecosystem fragmentation is one of the major factors driving biodiversity loss
today. This can occur by way of deforestation, construction of roads, fences and
buildings, land use changes, natural disasters, and climate change. Fragmentation is
clearly linked to habitat decline due to alteration of critical ecosystem processes such as
plant dispersal, plant community dynamics, plant and animal reproduction, and animal
movement patterns (Collinge, 2000). These processes become limited and altered as an
ecosystem is reduced to patches. The greater the distance between these patches, the
more unlikely cross pollination of separated plants or recolonization by lost species
becomes. The smaller the area of remaining contiguous habitat left, the greater the
likelihood of species extinction (MacArthur & Wilson, 1967).
Endemic species are especially sensitive to such trends. As we lose endemic
species, we lose the potential for further evolutionary steps towards recovery of
heterogeneous ecosystems (Wolf, 2001). Seed dispersal, as well as pollinator diversity


 

1
 

and abundance are heavily affected by fragmentation, and clearly impact endemic flora.
However, seed longevity and vegetative reproduction act as buffers allowing endemic
species to persist within small patches (Wolf, 2001). Regardless, as patches decrease in
area, limited resources will become monopolized by dominant species and diversity will
drop (MacDougall and Turkington, 2007). As fragments become smaller, the system is
more vulnerable to collapse due to trophic simplicity and single species dominance
(Collinge, 2000). The loss of ecosystem complexity pressures endemic species more
heavily as their range is finite and competition becomes increased.
Here in the Pacific Northwest, the South Puget Sound prairies are an ecosystem
suffering from fragmentation and non-native species invasion. These prairies are home to
many rare, endemic, and declining species, including four state-endangered species
(spsp.org). In Washington State, this ecosystem has been reduced to 2-4% of its historical
extent (Hegarty, Zabowski & Bakker, 2011). Restoration ecologists are using a variety of
techniques to combat the degradation of these prairies, but the results have been mixed
thus far.
One conservation organization, the Center for Natural Lands Management,
bolsters the prairie ecosystem using direct seeding and revegetation using plugs. The
purpose of this practice is to increase biodiversity and limit non-native species and
conifer encroachment. These treatments can be an effective means of increasing prairie
health, however limited seed sources and poor germination rates of both direct sown and
nursery raised seeds are limiting factors to potential success.


 

2
 

Although the limitations described affect plants from many families, the focus of
my research is on species of this distinction within the Poaceae family. They are
important early seral species, which colonize disturbed prairie sites, providing critical
food and cover for a variety of prairie fauna (Tollefson, 2006). They also play an
important role in erosion control, keeping valuable topsoil bound in their complex root
systems and protecting against soil transport by wind and water. These are some of the
first species to be planted out in prairie revegetation projects, and thus are an important
target for improved germination rates.
In order to understand what may be hindering germination of these plants, it is
critical to first understand their natural history. Fire regimes played a significant role in
the ecology of the region. Native Americans burned the prairies every 2-3 years for
millenia in order to easily collect food, fiber and medicine as well as to combat against
native conifer encroachment (Rook et al, 2011). This practice continued into the
nineteenth century until western colonizers imposed burn bans. The omission of annual
fire from this ecosystem is a serious change in the disturbance regime these plants
experience.
While the use of prescribed fire is a proven and effective means of prairie
restoration, there are a number of factors that make it unfeasible as a restoration tool
during certain seasons of the year. The major factors that limit the use of prescribed fire
are the number of people necessary to safely implement a controlled burn, the associated
costs of equipment and training for that crew, the litigation against burning during certain
seasons of the year, and its potential effectiveness in small-scale application. In response
to these concerns, this thesis will delve into the components of fire that contribute to

 

3
 

prairie regeneration and attempt to isolate one variable that may prove to be an effective
surrogate to be used in the instances where prescribed fire is not a viable option.
Recent studies have identified a class of compounds released in plant-derived
smoke called Butenolides. These compounds have been tested on 1,355 species of plants
from 120 families for their germination responses. Within Poaceae, 95 species (of more
than 10,000 species) have been tested, with 46 resulting in significant germination
increases (Jefferson, Pennacchio & Havens, 2014). Those that have been tested come
from a variety of ecosystems on six continents, with germination increases found
primarily in species of fire-prone ecosystems. Treatment of seeds for this purpose have
been applied both by aerosol smoke as well as plant-derived smoke water.
This thesis will explore whether the addition of plant-derived smoke water will
increase germination rates for six species of Poaceae that have a history of poor
germination in our nurseries. The seeds from each species were imbibed with plantderived smoke water during their stratification stage. The species I have chosen are
regularly grown for South Puget Sound restoration and represent some of the local
diversity in the Poaceae family.
My hypothesis for this experiment was that the addition of plant derived smokewater would increase the rate of germination for each species when compared to a control
of deionized water. My definition for germination is the emergence of a 2mm radicle
from the seed after germination is induced, by alternating light and temperature regimes.
I monitored germination for 35 days (5 weeks). In my literature review, I synthesize the
current science regarding all variables of my experiment including prescribed fire, seed


 

4
 

germination, germination cues related to fire, plant-derived smoke water, my study
species and future implications. The following chapters outline my materials and methods
for the experiment, summarize my results and discuss their potential causal factors, and
share the conclusions we can garner from this experiment.


 

5
 

Literature Review
Introduction
This thesis was inspired by my work as a conservation nursery coordinator with
the Sustainability in Prisons Project (SPP). We are partnered with the Center for Natural
Lands Management (CNLM) to raise plugs for the revegetation of the South Puget Sound
(SPS) Prairies. It is through this work that we identified the species of focus for this
thesis, which we have had difficulty growing in our nurseries from 2009-2015. The
literature on the SPS prairies as a threatened ecosystem is vast and well documented.
However, our knowledge of smoke-derived germination-inducing chemicals is relatively
recent, and is still becoming understood. This literature review details the basis for the
work we are doing in the SPS prairies and explores previous studies in the field of fire
ecology that motivated our decision to experiment with plant-derived smoke water as our
treatment.

SPS Prairie Environmental History
In order understand the energy and resources being put into prairie revegetation, it
will be helpful to understand the natural history of the current ecosystem as well as
historical changes in ecosystemic conditions that lead to the current state of the SPS
prairies. In particular, the disturbance regime today is completely altered from what was
experienced over the last five to seven thousand years (Rook et al., 2011). This change is
at the heart of how the ecosystem functions now as opposed to the thousands of years
prior to European arrival.


 

6
 

Historically, Native Americans burned these grasslands on a semi-annual basis
until colonists put into effect fire suppression practices. Fire served many purposes, both
culturally and ecologically. It was an effective means of control against encroaching
conifer saplings, as well as against many non-native herbs and grasses (Hamman et al.,
2011). Having open non-forested areas was advantageous for hunting, and the fires would
drive game into the open range (Kruckeberg, 1991). After burning the prairies, Native
Americans could more easily harvest plants used for food, fiber and medicine from the
soil (Dunwiddie & Bakker, 2011).
In the SPS prairie ecosystem regular fire return intervals act as a pulse
disturbance, where stand-replacing events reset the system back to an early successional
stage (Bender, Case & Gilpin, 1984). As the system regenerates, colonizing species are
the first to fill in the landscape, and tend to grow at a faster rate, as there is little
competition and an abundance of nutrients, light and space. Fires promote these plants’
ability to sprout, soil seed bank adaptations, and their ability to disperse seeds (Agee,
1996). The local tribes understood this process, and used it to their benefit. Not only did
fires encourage the growth of important forage species, but it also made collection and
harvest of these easier.
Burning the prairies specifically encouraged the growth of Camas (Camassia
quamash), which was a culturally important plant used for food and medicine
(Kruckeberg, 1991). But Camas was not the only native species of this region that
evolved adaptations to fire. Species of the genera Castilleja are fire adapted and were
used medicinally. Balsamorhiza deltoidea is a large flowering species that is promoted by
fire and whose seeds were eaten by many tribes. Solidago roots were used medicinally

 

7
 

for a number of maladies and sicknesses. Species of the Lupinus genera are also fire
adapted and were regularly used as a food source by tribes as well as Europeans.
As Native Americans used fire to improve hunting, manage the ecosystem and
increase supplies of food and medicine, the regular disturbances began to shape the
species makeup and successional trajectory of the region. Fire characterized the region by
opening up niche space, which in turn reduces single species dominance (Rook et al.,
2011). Over millennia, the SPS prairies became conditioned to regular disturbance by
fire. Prairie ecosystems are most limited by light, and therefore most affected by the
encroachment of fast growing shrubs and trees that can quickly rise above and shade out
shorter, slow growing native species (Tillman, 1997). Today some of the most prevalent
examples are invasive Scot’s Broom (Cytisus scoparius) and native Douglas Fir
(Pseudotsuga menziesii). And as a disturbance-dependent ecosystem, the break in that
disturbance pattern can pose a risk to the region as single species dominance can become
prevalent (MacDougall & Turkington, 2007).

Prescribed Fire
With the knowledge that stand replacing fires were a regular event in the SPS
prairies for millennia, yet are practically absent today, it follows that this ecosystem is
lacking components related to fire that could influence the imbalance we witness today.
Fires are recognized to maintain species diversity, eliminate non-native fire-intolerant
plants, remove allelopathic substances, increase light intensity, change nutrient cycling
and pH, as well as increase net primary production (Jefferson et al., 2008). Many of these


 

8
 

environmental conditions work in succession with each other and can produce convergent
properties that are more substantial than any taken individually. Due to these influences,
restoration ecologists working in the SPS prairies favor prescribed fire as a restoration
tool, when possible.
Managing the SPS prairies as an altered ecosystem today is a complex task that
incorporates controlled fire, herbicide application, mowing, tillage, grazing and manual
removal of non-native species. Controlled burns have become a major tool for prairie
restoration in this region (Rook et al., 2011). However, controlled burns can only be
administered under specific regulations and are also labor and equipment intensive. In
order to effectively use prescribed fire, managers must understand the scale that is
necessary for restoration, have a knowledgeable and collaborative burn team of at least
twenty five individuals, as well as proper programmatic and political backing (Hamman
et al., 2011). Prescribed fires pose the known risk of potential escape to surrounding
areas, which could cause substantial economic damage (MacDougall & Turkington,
2007). In addition to the known logistical challenges, a number of questions remain
regarding the consequences of using fire in this novel ecosystem.
The benefits from fire historically are clear, but whether or not those carry over to
SPS prairies in their current state remains to be seen. One unknown is prairie size, and
whether the use of fire can be effective at the small scale that many remnant prairies exist
in today. Stand replacing disturbances such as fire normally occur on a large scale
(typically >10ha). Therefore using such treatments in a habitat that is greatly fragmented,
having isolated patches smaller than 10 ha, could negatively affect rare plants and
animals that were formerly wide ranging, but now exist as an isolated, threatened or

 

9
 

endangered species (MacDougall & Turkington, 2007). Another unknown is the
potential germination of non-native fire adapted seed banks that could exist in the soil
(Rook et al., 2011). When an area has been invaded and the species makeup has shifted,
the seed bank can be as rich with invasive species as it may be with natives. While fire
can be an incredibly effective tool for restoration goals, it also poses many challenges,
which could be limiting depending on the scale of a restoration project.
Many of the benefits associated with fire are the product of a stand-replacing
disturbance. Exposure to light and bare soil, elimination of non-native plants and
elimination of single dominant species are all disturbance-based changes to grasslands.
But fire is unique from other forms of natural disaster with regards to the chemical
changes it can impart on a system. Its ability to remove allelopathic substances from soil,
cycle nutrients, and change pH are all evidence of chemical transformations that can
occur in and after a fire (Jefferson et al., 2008). But fires influence on seed germination is
an area of particular interest to this thesis.

Seed Germination
Seed germination is the first stage of plant growth and is one of the few
mechanisms for plant reproduction. Environmental variability is critical to this process
and largely controls how and when a seed may germinate. Moisture content, light
availability, soil chemistry, temperature regimes, seed viability and predation are all
factors that can work independently or in succession to promote or inhibit this process.


 

10
 

The manner is which these variables affect seed germination is dependent upon the seed’s
physiology.
Serotiny is one such physiological trait that can differentiate germination
mechanisms. It is defined as those seeds, often held in cones or fruit on trees, which
remain attached to their mother plant after seed maturation and, when released, are
immediately ready for germination (Baskin & Baskin, 2001). Serotinous seeds do not rely
on a state of dormancy prior to germination, and instead rely on environmental cues that
trigger their release from the parent plant. Conversely, non-serotinous seeds are released
at the time of maturation regardless of the environmental conditions and instead rely on
dormancy to remain viable in the soil bank until the proper conditions present
themselves. Non-serotinous seeds can wait months or years for the appropriate cues prior
to germination.
Dormancy within the soil bank is a trait only exhibited by non-serotinous species.
But in order to understand the type of dormancy, these plants can be further split into two
groups - those that possess a thick, hard, water and gas impermeable seed coat and those
that can readily absorb water. The species that have an impermeable seed coat experience
a state of physical dormancy. They are most likely to break this state by extreme heat
shock, generally caused in the natural environment by a fire (Keeley & Fotheringham,
1998). This occurs when the hard, water-impermeable, seed coat is cracked by heat and
water is allowed to penetrate and thus facilitate germination (Light, Daws & Van Staden,
2009). This cracking can also occur through freezing, extreme temperature fluctuations,
or passage through animal digestive systems.


 

11
 

The species that do not have an impermeable seed coat, such as those from the
Poaceae family, rely on a different mechanism to trigger their germination. They can
readily absorb water and have no limitations to gas exposure. Poaceae species tend to
experience nondeep physiological dormancy, which requires a chemical change to
promote embryonic growth (Baskin & Baskin, 2001). The most common chemical
changes are triggered through variation of moisture content, temperature and light
exposure. However, other mechanisms exist that can alter seed chemistry, and fire is well
documented to promote such chemical changes.

Fire and Germination
Documentation of seeds being treated with smoke prior to sowing date back to
1632, although the practice itself could be much older than the written record. This was
observed of the Huron people of New France, who suspended germination boxes with
soil and pumpkin seeds above their fires, which reportedly “increased the number of
sprouters” (Jefferson, Pennacchio & Havens, 2014). Since that initial observation, similar
instances of smoke-preparation of seeds have subsequently been witnessed of indigenous
people in South Africa and Guatemala. Fire and smoke have been ubiquitous throughout
human history, and practices of this nature have been prevalent throughout many
cultures. Nonetheless, formal studies of the association between fire and increased seed
germination are a relatively recent development.
One of the first published studies on the subject was in 1977, by D.T. Wicklow.
The experiment tested the seeds of Emmenanthe penduliflora with two treatments, one of


 

12
 

burned (3/4 charred) plant stem segments and the other of incinerated plant stem ash. The
seeds touching the burnt stems germinated while those covered in ash rarely germinated.
Burnt stems were then placed on ungerminated seeds that were previously used in the
control, and subsequently began to germinate. The take-away from this experiment was
twofold – there is an association between burnt plant material and seed germination, but
plant material that is completely incinerated does not garner the same effect.
Later the association between charred plant material and seed germination was
extended to smoke, which carries many of the same chemicals as the burnt plant material
itself. For the sake of experimentation smoke can be easier to control for than the
inconsistencies of charring plants uniformly. However, this shift does not show up in the
literature until 1990 when de Lange and Boucher observed significant increases in the
germination of Audouinia capitata after exposing the seeds to aerosol smoke. As traction
began to increase on the subject, studies from the Cape Floristic region of South Africa,
the Southwest Botanical Province of Western Australia, and the Californian Floristic
Province became prevalent as each are biodiversity hotspots with associated fire-prone
ecosystems (Jefferson, Pennacchio & Havens, 2014). Further studies have yielded
increased germination of species from Mediterranean, semiarid, arid, temperate,
subtropical and tropical regions.
As more articles became published, indicating a connection between smoke
treatments and increased germination, researchers began to investigate the mechanism
driving these results. Initial studies concluded that the stimulatory effect could be
produced by a wide variety of plant materials and is not dependent on light. It is water
soluble, active 24 hours after exposure, and can be produced at 175° C for 30 minutes

 

13
 

(Keeley & Pizzorno, 1986). It took researchers decades to investigate the thousands of
compounds that can be present in smoke. One study successfully isolated and tested
seventy-one different compounds, but none individually produced as significant of results
as aggregate smoke treatments (Baldwin et al., 1994).
Finally in 2004, two separate research teams independently identified a watersoluble compound, produced by the combustion of cellulose that stimulated germination
in lettuce seeds. One group (Flametti et al.) worked in Western Australia while the other
(van Staden et al.) was in South Africa. The product, later named karrikinolide (KAR1),
belongs to the butenolide class of compounds. Butenolides are documented to drive a
variety of biological activities, including “promoting and inhibiting seed germination,
inhibiting shoot branching, inducing hyphal branching in arbuscular mycorrhizal fungi,
toxicity and antibiosis” (Jefferson, Pennacchio, and Havens, 2014).
Since the discovery of KAR1, studies have been done in Australia, Europe, South
Africa, and the United States to test its effectiveness of increasing seed germination
(Reyes & Trabaud, 2008). Although many of these trials have shown positive results,
some tests of KAR1 exclusively, have not had the success that a plant derived smokewater solution had (Kulkarni et al., 2011). This is indicative of the number compounds
that can be found in smoke, and the fact that germination cues often compound upon each
other. Isolating an individual synthesized compound may not be as effective as a solution
that holds many compounds and thus, potentially, multiple cues for germination.

This is

the basis for our choice of testing plant-derived smoke water for our experiment.


 

14
 

While researchers have isolated butenolide compounds, and can synthesize KAR1
for more controlled applications, the specific mechanism of how it promotes germination
is still under investigation. It is hypothesized that there are similarities between the
effects of smoke and other plant growth regulators, such as gibberellins; both can
stimulate germination by substituting for red light (Light, Daws & Van Staden, 2009).
Subsequent research suggests KAR1 improves temperature and water potential range,
which in turn can increase germination rates (Kulkarni et al., 2011). In the decade since
its discovery, many theories have been posited, yet none have been fully substantiated as
to how specifically butenolides increase germination at a chemical level. Nonetheless, the
significant amount of research connecting smoke-treatments and increased seed
germination is undeniable, and, for the purposes of this experiment, will suffice.

Plant-Derived Smoke Water
Plant-derived smoke water is a solution used in experiments as well in
horticulture to control smoke application. Other forms of smoke application include
aerosol smoke, aqueous ash solutions, as well as directly smoking a plant or patch of
property with a large mechanized smoking apparatus and tenting. While aerosol
treatments of seeds have had negligibly better results in germination treatments, it is
accepted that smoke-water is a more realistic, less cumbersome mode of smoke
application for restoration purposes. (Kulkarni et al., 2011; Llyod, Dixon &
Sivasithamparam, 2000). Smoke water can be produced in large batches, stored easily,
and applied over a larger area of land with greater ease than the other methods of smoke
application.

 

15
 

Plant-derived smoke water is created by “bubbling smoke through a container of
water” (Light et al., 267). According to Light, Burger and Van Staden active compounds
are produced between 160° and 200° C, however higher temperatures may lead to
volatilization of those compounds (2005). To create smoke-water for this study, I will
follow the protocols laid out by Flematti et al., except I will use Quercus garryana for the
coals and the chaff from a native perennial in place of Banksia-Eucalyptus (2004). As of
now there is no standardization for smoke-water concentration. Although the production
methods are fairly universal, dilution rates range from 2:1 to 5000:1, depending on the
study (Brown and Van Staden, 1997). For this experiment we are using a 100:1 dilution,
based on the prevalence of its usage in the literature (Keeley & Fotheringham, 1998;
Kulkarn et al., 2011; Lloyd et al., 2000).

Smoke Treatments of Poaceae
According to Jefferson, Pennacchio & Havens in their meta-analysis on the
subject, 1,355 species of roughly 250,000 known plant species have been tested for some
reaction to aerosol smoke, smoke-water, or plant-derived smoke products (2014). These
plants range from six continents of the earth, and are native to both fire-prone regions as
well as areas that do not regularly experience pressure from fires. The majority of the
species that had reactions to these treatments were from Australia, South Africa,
California, and the Mediterranean region. There were wide ranging effects from
increased germination to decreased germination.


 

16
 

In the restoration of the SPS prairies, there is a moderate but critical dependence
on nursery raised plugs for revegetation purposes. The species that are chosen to start in a
nursery, as opposed to being directly sown in situ, are those that are either especially
difficult to raise, are rare and lacking abundant seed sources, or are especially valuable as
threatened species. Although transplanting plugs is not without its challenges, for some
species this is simply the only viable option. Different plants require a variety of growing
protocols in a nursery. Many require cold-wet stratification prior to sowing. Some require
scarification of their seed coat. And others have responded favorably to smoke-water
applications after sowing. Nursery managers are regularly looking for any edge that can
improve the germination rates, seedling vigor, and survivorship of the plants they raise.
This experiment is intended to improve the ex situ growth of a group of species that have
previously challenged us with their low germination rates.
Poaceae, the grass family, is a logical place to start in the restoration of
grasslands. Species from this family are the glue of the ecosystem, with their intricate
root systems that bind the earth together, preventing erosion and nutrient loss. Prairie
sites are first cleared of invasive and non-native species prior to transplanting native
plants. Poaceae establish quickly in their place and can jumpstart the trajectory of a
restoration project. The quick rise to maturation also allows for immediate forage and
habitat cover for native fauna, which creates a feedback loop as they help to further
spread seed and fertilize the area.
We found it fitting to do a survey of Poaceae responses to smoke water, as
grasses are generally well adapted to survive under frequent fire regimes. The species we
have chosen and were able to acquire seed for, represent a breadth of the native Poaceae

 

17
 

of this region. Although none of the six species targeted in this experiment have
previously been tested for a reaction to smoke treatments, other closely related species
from the family have yielded significant germination increases (Jefferson, Pennacchio &
Havens, 2014; Kulkarni, Light & Van Staden, 2011). In the meta-analysis on smoke
treatments to date, nearly half of the Poaceae species tested (46 of 95) produced such
results (Jefferson, Pennacchio & Havens, 2014). Undoubtedly, 95 species is hardly
representative of a family comprised of over 12,000, but smoke treatments have not been
widely documented to this point.

Study Species
Bromus carinatus is a medium-sized (45-120 cm) biennial or perennial
bunchgrass. It is found in western North American states and provinces from Alaska to
Baja California. It is found in cool moist woods and open meadows, from foothills to
mountains. It produces numerous seeds that mature in June and July. It is a competitive
species that establishes in disturbed environments quickly through high seed production.
It is a successful competitor of exotic and invasive species, and its fibrous root system is
great for erosion control. It provides nutritious and palatable forage for all species of
ungulates, specifically elk. Bear, geese and rodents also consume its foliage, while small
mammals and game birds consume the seed.
Danthonia californica is a medium-sized (30-100 cm) perennial bunchgrass. It is
native from British Columbia down through California and out east to the Rocky
Mountains. It is broadly adapted to woodland, shrubland, grassland, and transitional


 

18
 

wetland habitats. California oatgrass grows sporadically from seed due to dormancy and
competition. It flowers between May and early July. It is recommended for revegetation
and recovery of savannahs, oak woodlands, and prairies in the Pacific coast states. It
improves habitat by erosion control and invasive species competition. It also provides
food, nesting and cover for songbirds. Its foliage is eaten by certain species of caterpillar
and its grain is eaten by birds and mammals.
Dichanthelium acuminatum is a medium-sized (15-80 cm) perennial panic grass.
It is native throughout all of the United States and Canada and can be found in
woodlands, savannahs, prairies, glades and bluffs. It reproduces by seed only and
establishes best in early secondary succession, however its density drops a few years after
establishment. It flowers in June and then dies back, but often flowers again in
September. Tapered rosette grass is valuable for ecological restoration of disturbed sites
and is useful as a soil stabilizer. Moth larvae and the caterpillars of skippers consume its
foliage, while the seed is eaten by game birds and songbirds.
Dichanthelium oligosanthes is a medium-sized (30-60 cm) perennial panic grass.
It is native to all of the United States and Canada except Nevada and South Carolina. It
can be found in woodlands, savannahs, prairies and glades. Seeds are produced in June
and then again in September after the plants die off during the height of the summer.
Grasshoppers, moth larvae, caterpillars of skippers and beetles eat the foliage. The seeds
are eaten by game birds, songbirds, mice, rabbit and deer.
Elymus glaucus is a large (150cm) perennial bunchgrass. Blue wild rye is found
from Alaska to Mexico and east through the Great Plains. It is found in woodlands,


 

19
 

prairies and chaparral. The seeds develop from May through July. It is an effective
species for stream bank erosion and helps to colonize burned and disturbed sites. It is a
very fire tolerant species. Mammals, birds and waterfowl use it for habitat and forage.
Elymus trachycaulus is a medium sized (50-100 cm) perennial bunchgrass. This
short-lived (3-5 years) species is found across North America from Canada to Mexico,
with the exception of the southeastern United States. It is adapted to basic soils (pH 8.8)
as well as moderate salinity. However, it is not as tolerant of drought as other species in
the genus. The seeds are produced from late July through early August. Slender
Wheatgrass grows quickly as a seedling and is used for disturbed site reclamation and
erosion control. It is a pioneer species in both primary and secondary succession. Game
birds and small mammals consume the seeds and use this species for cover. Larger
mammals such as elk and big horn sheep readily graze this species due to its high crude
protein content.

Implications
With an understanding of the fire regime history of the SPS Prairies, we know
that the native species in the Poaceae family have experienced regular exposure to fire
and smoke throughout the last several millennia. In an effort to maintain, restore and
expand the prairie ecosystem in Western Washington, ecologists are augmenting the
ecosystem with native seeds as well as nursery-raised plugs. However, low germination
rates coupled with the rarity of many prairie plants (due to habitat loss) have challenged
prairie restoration efforts. That combination of challenges makes many of these species


 

20
 

seed-limited. Prescribed fire is an effective method for restoration, but is often resource
intensive. With the recent developments in our understanding of how butenolides and
other compounds from smoke can increase germination in plants from the Poaceae
family, I believe there may be a cost effective method to increasing the germination of
these seeds through the use of plant-derived smoke water. This study examines the
effectiveness of smoke water applications for six species of Poaceae.


 

21
 

Methods and Materials

 

Plant-Derived Smoke Water
Many researchers have used plant-derived smoke water for the same purpose as
this thesis. However, each study has a somewhat unique methodology for producing it, as
there is no set standardization in the field as of 2016. I worked with my SPP conservation
nursery crew to establish our methods, which required a few trial runs to calibrate the
equipment. The initial challenge was to produce a consistently thick smoke for the
duration of the process, while maintaining the temperature within the desired range. We
found that it was much easier to build up to the temperature threshold incrementally, than
to try and reduce the heat of the fire if it became too hot. In order to carefully control the
heat, we built our coals in a separate barbeque and added them into the smoker one at a
time. The following section describes how to build the smoker for optimum results.

Assembling the smoker
Figures 1.1 & 1.2 below are labeled to accompany the description that follows.
The process of creating plant derived smoke water is achieved using a modified meatsmoker [A] (we used a Brinkman Trailmaster BBQ - #081269 smoker). We removed the
chimney from the smoker and, in its place, attached a 3-foot long 1” stainless steel pipe
[B] to the exit vent. The pipe extends from the smoker horizontally and is held upright
using an H.D. jack [C] – similar to a car jack, but with a V-shaped crotch for the pipe to
rest in. The other end of the pipe was attached to a ¼” rubber hose [D] that was clamped


 

22
 

to a 5L aspirator bottle [E] full of deionized water. Atop the aspirator bottle we taped a
suction diffuser [F] - a broad plastic funnel with holes drilled in the sides. The diffuser is
then taped to a shop vacuum [G]. The suction diffuser allows a moderate level of airflow
to be pulled through the water without the vacuum actually taking any water in.

Figure 1.1 – Smoking Apparatus - Modified BBQ used to produce plant-derived smoke
water. The letters represent each individual part, and correspond to the paragraph above.
(See figure 1.2 for a more detailed diagram of parts D-G).


 

23
 

Figure 1.2 - Smoker parts D-G. Close up
diagram of the 5L aspirator bottle attached to
the vacuum. The letters correspond with the
paragraph above.

Operation of the smoker
Once the smoking apparatus was put together we built coals in a separate grill (a
Weber Smokey Joe 14” charcoal grill). We used a separate grill so we could add a single
coal at a time in order to precisely control the heat in the smoker. The coals were made
from chunks of Quercus garryana wood. We started by placing a few coals into the
smoker until we got the temperature above 65° C. In order to produce smoke, we placed
the chaff from native Symphyotrichum hallii and Seriocarpus rigidus onto the coals.
Chaff is the leftover husks, stems, leaves and straw from plants that have been harvested
and cleaned to separate out the seeds. If the temperature became too hot (above 90° C)
we would add chaff, of the same two species, that had been soaked in water. We used


 

24
 

native oak and chaff over store bought charcoal and wood chips to ensure that all
compounds in the smoke were those that would be found in a prairie ecosystem. Once we
had produced a thick smoke, we turned on the vacuum to pull the smoke through the
deionized water. In order to maintain the high end of the heat threshold, we would add in
coals one at a time throughout the process. To maintain a steady thick smoke, and to keep
the temperature from elevating too quickly, we would add dry chaff followed by wet
chaff. This process continued for one hour, after which the water had become saturated
with smoke. The final product was transferred to 500 mL plastic bottles, labeled and
stored in a lab freezer at 0° C.

Study Species
All of the seeds used in this experiment were collected at maturity from a number
of sites around South Puget Sound (Table 1). The seeds of B. carinatus and E.
trachycaulus were wild collected from Joint Base Lewis-McChord, site R76, in the
summer of 2015. The seeds of D. californica were harvested from Webster’s seed farm
(Maytown, WA) in the summer of 2014. The seeds of D. acuminatum and D.
oligosanthes were harvested from Shotwell’s Landing seed farm (Littlerock, WA) in the
summer of 2015. And the seeds of E. glaucus were harvested from the Violet Prairie seed
farm (Tenino, WA) in the summer of 2015. After collection and harvest, all seeds were
cleaned at Shotwell’s Landing, and stored in paper envelopes at 5° C in a seed storage
refrigerator until they entered stratification for this experiment.


 

25
 

Table 1. Seed collection origin. The table lists the species codon, lot number, collection year,
collection location, site name, and site type.

Experimental Design
The methodology for ecologically meaningful germination studies is outlined in
chapter 2 of “Seeds” by Baskin & Baskin (1998), and is the protocol used in this
experiment. They recommend using intact natural dispersal units, however our seeds lost
their palea and lemma in the seed cleaning process. This is the condition of the seeds that
are used by restoration ecologists, and as such I wanted to maintain continuity with what
is being used in the field for this experiment. Baskin & Baskin defer to Dr. Lela V.
Barton on the case of replication, recommending 3 replicates of 50 seeds per treatment.
We will be using 10 replicates of 50 seeds per treatment in order to strengthen our results.
Our experiment had separate phases, first a stratification period, followed by a
germination period (Table 2).

Table 2 – Experiment Time Table - Stratification period and germination period duration for
each species, in days (SPP Conservation Nursery Manual, 2014).

26
 


 

 

Seed stratification
Seeds for each of our species require cold stratification to achieve optimum
germination. Cold stratification is the emulation of winter conditions, where the seeds are
placed on a wet substrate and stored in a cold environment equal to the average
temperature of their native winter ecosystem. Every species responds differently to
stratification length. For the purpose of this experiment, we are using the stratification
protocols used by SPP in their nurseries (Table 2). This will allow for a comparison of
our germination results with their nursery data from 2009-2015. We used a germination
chamber for both the stratification period and the germination period. This was an ideal
tool for the experiment as the lights and temperature can be manually changed as needed
and then maintained by timers.
The seeds for each of my six species were split into sets of 50 seeds. Each seed
was examined on top of a light table and under magnification to determine that they were
fully formed. Once split into sets, each set was placed into a sterilized petri dish on top of
two pieces of filter paper (double-rings 90mm). One replicate was a set of 50 seeds. Each
species had ten control replicates and ten experimental replicates. The total number of
seeds for each species was 1000. The control replicates were imbibed with 3mL of
deionized water. The experimental replicates were imbibed with 3mL of a 1:100 solution
of plant-derived smoke water and deionized water. All 120 replicates were randomized
and then placed into a darkened germination chamber (SG30 Controlled Environment
Chamber) set at 2° C. After 24 hours all replicates were rinsed with 2mL of deionized
water and returned to the germination chamber.


 

27
 

Seed germination
After the stratification period ended, the germination chamber was reset to
alternate its temperature from 10° C with no grow lights for 12 hours, followed by 20° C
with grow lights (40 µmol photons m-2 s-1 PPFD) for 12 hours. This alternation of light
and temperature emulates spring conditions in order to trigger germination responses in
the seeds. During this germination period, each replicate was removed and opened to
survey for germination. Germination in this experiment is defined by the emergence of a
2mm radicle – the embryonic root (Figure 2). Once identified, the number of germinated
seeds per sample was recorded for that day, and those seeds were then removed to
eliminate duplicate counting in the future. This process was repeated every other day
during a 35-day germination period.

Figure 2 – Emergent Radicle Germination is defined by the emergence
of a 2mm radicle, or embryonic root.


 

28
 

Data Analysis
We analyzed the data from this experiment using JMP software. We ran a oneway ANOVA to determine whether the difference of means between each treatment was
statistically significant for each species. The mean for each replicate was determined as a
percentage of x/50 germinated seeds. We also calculated the time to 50% germination
(t50) for each treatment of every species. The mean t50 between treatments determines a
difference in seedling vigor as a measurement of growth speed. For all tests, statistical
significance was determined based on p < 0.05.


 

29
 

Results
Germination Rates
Elymus glaucus
Plant-derived smoke water increased germination rate significantly (p < 0.029) for
one of the six study species, Elymus glaucus (Figure 3.1). This data was especially telling
when you look at table 3.1 and see 6/10 experimental replicates had germination rates
equal to or above 90%. None of the control replicates reached 90%. Also only one of the
experimental replicates was below 50%.

Figure 3.1 Germination responses by E. glaucus to plant-derived
smoke water treatments. Each box and whisker plot represents the
distribution of the data, and x-bar indicates the mean. Significance
was determined based on p < 0.05.
 

Table 3.1 Germination
percentages for each replicate
of E. glaucus


 

30
 


 

 

Elymus trachycaulus
Plant-derived smoke water did not significantly increase germination rates for E.
trachycaulus (p < 0.199). The spread of the data was very low for this species, especially
in the experimental group. Smoke water appears to have had a very uniform effect on the
experimental treatment group, with 9/10 replicates within the 64-70% germination range.
The control group had a little more variability, and a higher ceiling with half of the
treatments achieving a greater germination percentage than the highest experimental
replicate. But both groups produced germination rates over 50% across the board.

Figure 3.2 Germination responses by E. trachycaulus to plant-derived
smoke water treatments. Each box and whisker plot represents the
distribution of the data, and x-bar indicates the mean. Significance

 
was determined based on p < 0.05.
 


 

Table 3.2 Germination
percentages for each replicate
of E. trachycaulus


 


 


 

31
 

Dichanthelium oligosanthes var. scribnerianum
Plant-derived smoke water had no significant increase in germination for D.
oligosanthes var. scribnerianum, (p < 0.245). The difference in means here is higher than
for any of the other non-significant species. However, the range of the data is also one of
the highest in this experiment. The smoke water group has an especially large range,
including an outlier of 0% germination. Overall the means here seem representative of
the spread of the data. The high variability of the smoke water group interests me for
further research.


 
Figure 3.3 Germination responses by D. oligosanthes to plant-derived
smoke water treatments. Each box and whisker plot represents the
distribution of the data, and x-bar indicates the mean. Significance

 
was determined based on p < 0.05.
 


 


 


 

Table 3.3 Germination
percentages for each replicate
of D. oligosanthes


 

32
 

Danthonia californica
Plant-derived smoke water did not significantly increase germination for D.
californica, (p < 0.335). The average germination for these two groups is very close, and
overall the spread of the data is very similar for both groups. The smoke water treatment
yielded one replicate with a particularly high germination percentage appears to be the
only minor difference. Both treatments produced germination rates above 60% across the
board.


 
Figure 3.4 Germination responses by D. californica to plant-derived
smoke water treatments. Each box and whisker plot represents the
distribution of the data, and x-bar indicates the mean. Significance

 
was determined based on p < 0.05.
 


 


 

Table 3.4 Germination
percentages for each replicate
of D. californica


 

33
 

Dichanthelium acuminatum var. fasciculatum
Plant-derived smoke water did not significantly affect the germination of D.
acuminatum var. fasciculatum, (p < 0.336). This species had consistently low
germination overall.

Figure 3.5 Germination responses by D. acuminatum to plant-derived
smoke water treatments. Each box and whisker plot represents the
distribution of the data, and x-bar indicates the mean. Significance

  was determined based on p < 0.05.
 


 

Table 3.5 Germination
percentages for each replicate
of D. acuminatum


 
 

 

Bromus carinatus
Plant-derived smoke water did not significantly affect the germination of B.
carinatus, (p < 0.396). The range of data some high for both treatments, but the majority
7/10 of the replicates yielded similar rates (< 16% difference) within each treatment. This


 

34
 

is the only species where the control treatments yielded higher individual germination
rates across the board. 8/10 control group treatments had a germination rate above 50%.

Figure 3.6 Germination responses by B. carinatus to plant-derived
smoke water treatments. Each box and whisker plot represents the
distribution of the data, and x-bar indicates the mean. Significance
was determined based on p < 0.05.
 


 
Table 3.6 Germination
percentages for each replicate
of B. carinatus.


 

Germination Rates Compared with SPP and the Literature
The basis for this experiment was the challenge SPP has had growing these
species as plugs from 2009 – 2015. I compiled their data below as compared with my
own control and experimental average germination rates (Table 4). I also included
germination data from the Native Plant Network (NPN), from the closest reports I could
find to western Washington. Laboratory based germination tests of these species were not


 

35
 

available in the literature. Both the SPP and NPN data are based off of the total number
of plants as compared to the number of seeds planted in plug trays. This data is only an
approximation and is used here a proxy for comparison sake.
Four of the five applicable control group averages from this experiment are higher
than the SPP averages. However, only two of the five applicable control group averages
are higher than the NPN literature. E. glaucus, the only species with a statistically
significant increase in germination from my experiment, also has a higher rate than either
SPP or NPN data.

Table 4 – Germination rates as compared with the literature - Germination rates (%) of the control (C)
and experimental (E) groups from this study compared with data from the Sustainability in Prisons
project (SPP) from 2009-2015, and literature from the Native Plant Network (NPN) and the location
and year of those studies.


 
Vigor

According to Soltani et al., the t50 metric is a valuable way to understand the
effects of treatments on seedling vigor (2015). The t50 statistic, time to 50% germination,
was calculated for all applicable species. No significant difference in vigor was observed
between the control and experimental treatments for any species (Table 5). Each
treatment reached 50% germination within 2 days of the other (out of 35 days) for all
species.


 

36
 

Table 5 – Time to 50% Germination (t50) - This table shows mean number
of days to 50% for each treatment of each species that reached at least
50% germination. One standard deviation is given below each mean;
outliers disproportionately skewed some of the data. The experiment
length was 35 days (5 weeks).


 


 

37
 

Discussion
Plant-Derived Smoke Water
The data from this study indicates that there may be a relationship between plantderived smoke water and increased germination rates for E. glaucus. The one-way
ANOVA showed a statistically significant difference of means between the 10 control
samples and the 10 experimental samples. This could bode well for future plantings of
the species in nursery settings. For plug production, smoke water could be applied either
at the time of seed stratification or immediately after sowing. The other five species did
not yield significant differences in germination rates between the control and
experimental groups. This could be due to a number of factors, which will be discussed in
the subsequent sections.

Overall Germination Compared to the Literature
Although only one out of six species showed significant differences between the
control and the experimental groups, it is worth noting that four out of five species had
greater germination rates in the control group than previously attained in nursery
plantings by SPP from 2009 to 2015 (Table 4). Furthermore, the control groups also
improved upon the reported germination rates of two out of the five species there is
germination literature on in the Native Plant Network (NPN), one of the most
comprehensive online databases regarding native plant propagation. This is valuable in
and of itself, as the goal of this study is to improve germination rates for the purpose of


 

38
 

restoration, regardless of whether the improvement comes by way of smoke water
applications.

E. glaucus
The overall germination rates for both treatments were greater than those
observed by SPP and researchers in Glacier National Park. SPP raised this species on and
off from 2009 through 2015, and their average germination rate for E. glaucus over that
period was 20% (Carl Elliott, personal communication). According to the NPN, a nursery
in West Glacier, MT recorded 40-50% germination for the species (Luna et al., 2008).
Our own research yielded a 61.4% average germination rate for the control group, while
the smoke water treatments increased that to 81%. It would follow that the conditions
provided in this experiment (temperature and light settings, stratification length, and the
addition of plant-derived smoke water) all contributed to increased germination when
compared with the literature as well as the control group.

D. californica
The overall germination rates for both treatments were greater than those
observed by SPP and a nursery in San Francisco, CA. SPP raised D. californica on and
off from 2009 through 2015, and their average germination rate for the species over that
time was 10% (Carl Elliott, personal communication). According to the NPN, a nursery
in San Francisco, CA averaged 60% germination when raising this species (Young,
2001). The results of this experiment yielded a 79% germination rate for the control


 

39
 

group, and an 82.6% rate for the experimental group. The difference between the control
and the experimental groups are negligible, but I would recommend following the
stratification length and temperature and light splits chosen for our control treatment to
attain this high rate of germination in future plantings.

E. trachycaulus
This particular species behaved different than the majority of the others. The
germination rate for the experimental group, at 66.8%, was lower than that of the control,
70.6%. Once again, the difference between the two is negligible at < 5%, but it appears
clear that smoke-water is not a driving factor for germination of this species.
Nonetheless, the control group germination rate is still an improvement over the average
rate recorded between 2009-2015 by SPP, which was 20% (Carl Elliott, personal
communication). The protocols used in this experiment should be considered for future
sowing of E. trachycaulus in Western Washington.
It is worth noting that a nursery in Bridger, MT was able to achieve a 92%
germination rate when growing this species (Winslow, 2002). But it can be difficult to
compare the growing conditions in Eastern Montana with those of Western Washington,
which we modeled the temperature fluctuation used in our germination chamber after. I
will discuss the variable of differing temperature regimes below, but that may be a factor
worth considering when comparing the robust germination found in Montana with the
moderate success of our control group.


 

40
 

D. oligosanthes
This species has very little literature published regarding its propagation. SPP has
attempted to grow it from 2009-2015 and only yielded a 5% average germination rate
(Carl Elliott, personal communication). This experiment did not bring much clarity to the
challenge of growing D. oligosanthes. The control group averaged 28.2% germination,
while the experimental group did slightly better at 38.8%. The one-way ANOVA did not
find the difference between the two to be statistically significant. However the JMP
software determined one value to be an outlier in the experimental group. After omitting
the outlier, the average germination rate improved to 43.1%, while the p-value from the
one-way ANOVA changed from p < 0.245 to p < 0.085. This is still not significant but
intrigues me regarding future research.
D. oligosanthes is somewhat of a mystery when it comes to growing protocols.
SPP fared poorly in raising it, the NPN had no entries regarding growing it, and I would
not say 38.8-43.1% germination rate for our experimental group is particularly strong
when projecting out for prairie restoration. It is hard to evaluate the data from this
particular species as the average rate appears accurate overall, but there are also extreme
high and low individual replicate values in the experimental group (Table 3.3).
Due to the ambiguity of the results, I would like to see this species tested further
for smoke and fire related treatments. One consideration is the complexity of germination
cues that result from fire. Many of these cues compound upon each other to produce ideal
germination conditions. Maybe this is a scenario where smoke water coupled with
another fire-related cue could result in a significant increase in germination. Looking at
the individual replicate values, its obvious that the experimental group improved

 

41
 

germination rates over the control, albeit negligibly in most cases. I would still suggest
nursery managers to consider further experimentation with smoke-water when growing
this species as all other documentation reports extremely low germination rates
comparably. Another consideration would be a longer stratification period. For this
experiment we used a 15-day stratification length, but future researchers may want to
experiment with 30, 45, 60 and 90-day stratification intervals as well.

B. carinatus
This was the other species from this experiment whose germination rate decreased
from the control (54.6%) to the experimental group (48.2%). Once again, the difference
between the two groups is not significant. A high germination percentage of 54.6% is
acceptable for nursery growing purposes, but not ideal. SPP has no previous records of
the germination rates for this species, so the only comparison available is the nursery
from Bridger, Montana. According to the NPN, they achieved a 91% germination rate,
which is certainly greater than anything in this experiment (Winslow, 2002). I will
maintain the same caveat I mentioned earlier regarding the difference in climate between
eastern Montana and western Washington.
Upon further research, I found a U.S. Forest Service document describing the
geographic differences in growing B. carinatus. According to their literature, this species
has been reported with germination rates of 89% when grown in the southwestern U.S.,
85% in Montana and 48% in Oregon. This was followed up with data from a greenhouse
experiment that yielded 85% germination when the temperature fluctuated between 20°


 

42
 

and 30° C. They then lowered the average temperature to 14° C and the germination rate
dropped down to 46% (Tollefson, 2006). This aligns with both the results from our
experiment, and the data from the NPN. Unfortunately, with limited time for this
experiment and only one germination chamber, we were only able to set one temperature
regime for all six species. But I would suggest that in future trials the 20° to 30° C range
be used for B. carinatus. Also, for nursery managers in western Washington attempting to
grow this species, early summer sowing may produce the best results.

D. acuminatum
This species had the lowest overall germination rate of the six, with a control
group average of 7.4%, and experimental group average of 9.4%. SPP did not fare much
better in their attempt to grow D. acuminatum, as they only reached 15% germination
(Carl Elliott, personal communication). The NPN has a listing from Corvallis, OR that
yielded a 30% germination rate for the species (Bartow, 2007). None of these numbers
are ideal for restoration purposes. It seems there is some factor yet to be explained that
holds the potential for increased germination of this species. I would highly recommend
more research to explore the alternatives, but this experiment does not provide much of a
starting point of where to look regarding this species.
According to data published by the US Forest Service, D. acuminatum increased
in frequency in burned sites as opposed to unburned sites. However, the frequency was
greater in sites burned annually, and moderate in sites burned periodically. Other data
from the same report observed that D. acuminatum was one of the established species


 

43
 

most negatively affected by a 15-year fire in post-burn plant surveys (Walsh, 1995). This
information would suggest that minor to moderate intensity fires may improve overall
growth for this species, but it may also be vulnerable to higher intensity irregular fires.
Smoke water alone did not seem to affect this species growth, but maybe moderate heat
shock would improve its germination rates.

Controlled versus Variable Growth Environment
The motivation for this experiment was based from the low germination rates
from the SPP conservation nurseries. The laboratory based germination test was done in
order to isolate germination as clearly as possible. But the majority of the application of
this data will end up being used back in the variable environment of a greenhouse or the
prairies. While this experiment yielded increased germination rates over those previously
observed by SPP for D. californica, D. oligosanthes, E. glaucus, and E. trachycaulus, it is
important to acknowledge that this controlled environment eliminates a number of factors
at work in an outdoor nursery. For this experiment, the seeds received thorough moisture
throughout the germination phase, precise light and temperature changes, and were not
encumbered by pests, pathogens, or weeds. All of these factors can contribute to lower
germination rates in a nursery and should be considered when comparing the data from
this experiment with germination data from a nursery. This experiment will not tell us
specifically whether the lower germination rates from the SPP nurseries are due to
external factors, but will only allow us to understand the effect of smoke water on
germination and how germination-limited each species may be.


 

44
 

Nonetheless, it is beneficial to recognize the potential of each species in a
controlled setting and then begin to isolate the other factors that could be holding the
germination rates back. This could include predation by pests, competition by other plant
species that find their way into the same tube, seasonal conditions based on time of
planting or climate change, and simply length, frequency and duration of watering
regimes chosen during the germination stage. Knowing the ceiling for a species
germination rate with all other factors even is a foundation to build upon, but it is
unrealistic to assume the same results could immediately be achieved in a plug tray as
opposed to a petri dish. Future research will be beneficial to further our understanding of
external variables.

Seed Limitations
Another factor worth addressing is the seeds themselves. Seed source is incredibly
important in restoration. It is used for the purposes of tracking genetic lineages and
knowing which seed lots produce the hardiest plants. It is also critical for creating
heterogeneous ecosystems and not propagating genetic bottlenecks. For this experiment
we only used one seed lot per species, so the comparison of control seeds to experimental
seeds is accurate for evaluating the difference in treatments. However, the seed lots used
in this experiment were not the seed lots used in the SPP records, nor those used in any of
the NPN reports. Intra-species variation for plant varieties can differ significantly. For
example, this season SPP is growing 8 different lots of Castilleja hispida – some of the
seed lots have produced 0% germination and others are as high as 75%, with the rest
somewhere in the middle. The results produced in this experiment may vary greatly from

 

45
 

another identical experiment using seed sourced from another location. Seed viability can
decrease with age as well, and is another consideration to take into account when
comparing this study with former or future studies in the same vein. All of these seeds
were collected or harvested by the Center for Natural Lands Management (Table 1).

Germination Cues from Fire
Fire can influence seed germination through a variety of chemicals, temperature
fluctuations, water and nutrient availability, and exposure to light. Many of those cues
work in succession with one another to provide ideal growing conditions for fire-adapted
seeds. In this experiment, we controlled for each of those variables except plant-derived
smoke water. The results of this study did not yield significant germination differences
for five of the six species when exclusively adding smoke-water. However, there were
minor increases for some species, specifically D. oligosanthes and E. trachycaulus, and
such changes may not be coincidental.
Heat has been tested in conjunction with smoke treatments in much of the
literature on the subject. But there is no clear consensus about the role heat plays when
partnered with smoke. In one study of three native Lupinus species from SPS prairies, L.
Lepidus seeds had significantly increased germination rates when immersed in 80° C
water. Variable heating followed by cooling regimes to emulate spring conditions also
demonstrated germination increases for the other two Lupinus species (Elliott, Fischer &
LeRoy, 2011). For some species, temperature regime changes alone are enough to
stimulate germination.


 

46
 

Another study examined six South African grassland species and their
germination and growth when exposed to smoke water and butenolide concentrates at
different temperatures. The germination results showed few trends between species,
except for all species the overall germination rates increased in all treatment groups as the
temperature increased; and for five of the six species, germination peaked between 25
and 30° C. They also measured the shoot and root growth of each treatment group at 15°,
20°, 25°, 30°, 35°, and 30°/15° C for each species. In the smoke water treatment group,
five of the six species had a steady increase of growth as the temperature increased until
peaking at 30° C and then dropping off. The same trend occurred in the control group,
but with lower overall measurements (Ghebrehiwot et al., 2009). This demonstrates that
heat can impact germination on its own, but can increase that effect when paired with
smoke for species from fire-prone grasslands.
A separate study of 34 species from the California chaparral compared a control
group, heat shock treatments of 105° and 115° C, a 5% charred wood aqueous leachate,
and aerosol smoke treatments of 5 and 8 minutes. Seeds of each species were exposed to
all treatments in order to measure germination rate. The smoke treatments in this
experiment only raised the temperature in the treatment chamber 1° to 2° C above the
ambient room temperature, so the purpose of this was to isolate heat treatments from
smoke treatments. 22 of their 34 species had a statistically significant (p < 0.001) increase
in germination from smoke exposure. They found heat shock to have no stimulatory
effect for these species. Charred wood treatments also induced germination, but not as
significantly as the smoke treatments. In some cases, the 8 minute smoke exposure


 

47
 

produced a lethal effect (Keeley and Fotheringham, 1998B). The results of this
experiment are somewhat counter to those of the South African study.
Each of these studies provides a different example of how heat-shock,
temperature regime changes, and smoke-treatments can all work individually or
compounded with one another to affect germination and seedling vigor. They each
produced varying results that do not necessarily align with one another. But the purpose
in all of these is to attempt to represent each of the variables present in a wild fire. Heat,
burnt plant material and smoke all have been observed in some instance to increase seed
germination. Each of these variables should be researched further for their affects on the
germination of SPS prairie species.

Temporal Conditions
Time of year is controlled for in this experiment by use of a germination chamber,
but the temperature fluctuation of 10° C to 20° C could also play role in the overall low
germination rates for a few of the species, specifically D. acuminatum and D.
oligosanthes. The temperature range chosen for this experiment was meant to emulate
spring conditions. Both Dichanthelium species set their seeds in spring but often have a
second flush in late summer (August-September). So perhaps a ceiling of 30° C could
prove to be more beneficial for these species. If this were to have an impact it could alter
the time of year nursery managers choose to sow their seeds for restoration.


 

48
 

Conclusion
The SPS prairie ecosystem is unique in its dependence upon humans for
management. They were first formed from the glacial outwash approximately 10,000
years ago (Hegarty, Zabowski & Bakker, 2011). As the conditions turned more mesic a
few millennia later, conifers began to encroach into the lowland savannahs. The Native
Americans present at the time began to burn the grasslands on a three to five year interval
in order to stop the conifer encroachment, allowing the people to hunt and forage in the
open prairies. But regular burning stopped in the mid nineteenth century due to
suppression by European Americans. The combination of development and climate
change over the next 150 years further fragmented the prairies and altered their species
makeup. The prairies we are left with today occupy less than 5% of their previous extent,
are in poor health, dominated by non-native species, and lack diversity. The human
influence on this system cannot be overlooked. The SPS prairies flourished due to human
intervention, and are now seriously threatened due to human intervention. The future of
this ecosystem is in our hands today.
Regular fire-return intervals play a critical and complex role in the SPS
ecosystem. And the regeneration of the prairie sites on Joint Base Lewis-McChord
(JBLM), where burn regulations are much more flexible, is a testament to the positive
impact fire can have on the diversity of the system. Unfortunately, JBLM does not house
all the prairie sites left in the northwest. And the sites outside of the military base are
limited by seasonal conditions and state law, both of which restrict prescribed burns to a
few months each year. Although a site may only require burning once every five years to


 

49
 

have a positive impact, this still may not be feasible based on the resources, training, and
manpower necessary to execute a safe and effective burn.
The purpose of this study was to explore a supplemental avenue to controlled
burns. Restoration organizations are already working year round to produce seed, raise
plugs, and regrow the SPS prairies as quickly and efficiently as possible. But many of the
species are conditioned to certain disturbances that cannot be emulated in nurseries.
Plant-derived smoke water provides one channel to possibly unlocking the germination
potential in these fickle species.
Our hypothesis that smoke water would increase germination for six native
species from the Poaceae family was not realized. E. glaucus was the lone species that
appears to have a positive relationship with smoke water treatments, and I would
recommend to any manager raising this species, either in a nursery or direct seeding into
the prairie, that they incorporate smoke into that process in some capacity. As for the
other species, there is more research left to do. We yielded healthy germination rates in
our control group for D. californica and E. trachycaulus, at 79% and 70.6% respectively.
Those two species can theoretically get sufficient germination following the control
protocols of this paper. B. carinatus appears to be a species that prefers a warmer climate
than we have in western Washington for most of the year, so summer sowing or heated
greenhouse propagation may be the best avenue to increase its germination rate. D.
oligosanthes may well respond to multiple cues from fire and should be explored further
with smoke-water as well as heat shock tests. D. acuminatum is reported to occupy post
burn sites, but may be vulnerable to high intensity fires. Experimentation with different
stratification lengths coupled with moderate heat shock and smoke-water treatments may

 

50
 

yield better results. But it is clear by looking at these six species alone, that ecologists
cannot paint with broad strokes when propagating prairie species for restoration.
The positive takeaway from this research is that four of these six species are not
germination limited, when aiming for a germination rate above 50%. Growing these
species in plugs is a separate challenge, and should be further studied. For the other two
species, it is very helpful to recognize that germination is a limiting factor, even in a
controlled environment. They may not be economically viable to continue producing
until the key to their germination limits are understood. This study can be used to more
effectively produce B. carinatus, D. californica, E. glaucus, and E. trachycaulus, and can
be a springboard for future research focused on D. acuminatum and D. oligosanthes.


 

51
 

Bibliography
Altman, B. (2011). Historical and current distribution and populations of bird species in prairieoak habitats in the Pacific Northwest. Northwest Science, 85(2), 194-222.
Baldwin, I. T., Staszak-Kozinski, L., & Davidson, R. (1994). Up in smoke: I. Smoke-derived
germination cues for postfire annual,Nicotiana attenuata torr. Ex. Watson. Journal of
Chemical Ecology,20(9), 2345-2371.
Bartow, Amy. 2007. Propagation protocol for production of Container (plug) Panicum
acuminatum Sw. plants USDA NRCS - Corvallis Plant Materials Center Corvallis,
Oregon. In: Native Plant Network. URL: http://NativePlantNetwork.org (accessed
2016/05/01). US Department of Agriculture, Forest Service, National Center for
Reforestation, Nurseries, and Genetic Resources.
Baskin, C. C., & Baskin, J. M. (1998). Seeds: Ecology, biogeography, and evolution of
dormancy and germination. San Diego, CA: Academic Press.
Bender, E. A., Case, T. J., & Gilpin, M. E. (1984). Perturbation experiments in community
ecology: Theory and practice. Ecology, 65(1), 1-13.
Buisson, E., Holl, K. D., Anderson, S., Corcket, E., Hayes, G. F., Torre, F., … Dutoit, T. (2006).
Effect of seed source, topsoil removal, and plant neighbor removal on restoring
California coastal prairies. Restor Ecology, 14(4), 569-577. doi:10.1111/j.1526100x.2006.00168.x
Busby, L. M., & Southworth, D. (2014). Minimal persistence of native bunchgrasses seven years
after seeding following mastication and prescribed fire in Southwestern Oregon,
USA. Fire Ecology, 10(3), 63-71. doi:10.4996/fireecology.1003063


 

52
 

Collinge, S. K. (2000). Effects of grassland fragmentation on insect species loss, colonization,
and movement patterns. Ecology, 81(8), 2211-2221.
DeLange, J. H., and C. Boucher. 1990. Autecological studies on Audouinia capitata (Bruniaceae)
I. Plant-derived smoke as a seed germination cue. South African Journal of Botany, v. 56,
no. 6, p. 700-703.
Elliott, C. W., Fischer, D. G., & LeRoy, C. J. (2011). Germination of Three Native Lupinus
Species in Response to Temperature. Northwest Science, 85(2), 403-410.
Flematti, G. R. (2004). A compound from smoke that promotes seed
germination. Science,305(5686), 977-977.
Hamman, S. T., Dunwiddie, P. W., Nuckols, J. L., & McKinley, M. (2011). Fire as a restoration
tool in Pacific Northwest prairies and oak woodlands: challenges, successes, and future
directions. Northwest Science, 85(2), 317-328.
Harris, J. G., & Harris, M. W. (1995). Plant identification terminology: An illustrated glossary.
U.S.A: Spring Lake Publishing.
Hickey, M., & King, C. (2000). The Cambridge illustrated glossary of botanical terms.
Cambridge: Cambridge University Press.
Hopkins, W. G., & Hüner, N. P. (2004). Introduction to plant physiology. Hoboken, NJ: J.
Wiley.
Jefferson, L. V., Pennacchio, M., Havens, K., Forsberg, B., Sollenberger, D., & Ault, J. (2008).
Ex situ germination responses of Midwestern USA prairie species to plant-derived
smoke. American Midland Naturalist, 159(1), 251-260.


 

53
 

Jefferson, L. V., Pennacchio, M., Havens-Young, K., & Sollenberger, D. (2014). Ecology of
plant-derived smoke: Its use in seed germination.
Keeley, S. C., & Pizzorno, M. (1986). Charred Wood Stimulated Germination of Two FireFollowing Herbs of the California Chaparral and the Role of Hemicellulose. American
Journal of Botany, 73(9), 1289-1297.
Keeley, J. E., & Fotheringham, C. J. (1998). Smoke-induced seed germination in California
chaparral. Ecology, 79(7), 2320. doi:10.2307/176825
Keeley, J., & Fotheringham, C. (1998). Mechanism of smoke-induced seed germination in a
post-fire chaparral annual. Journal of Ecology, 86(1), 27-36.
Klopf, R. P., Baer, S. G., & Gibson, D. J. (2013). Convergent and Contingent Community
Responses to Grass Source and Dominance During Prairie Restoration Across a
Longitudinal Gradient. Environmental Management, 53(2), 252-265.
Kruckeberg, A. R. (1991). The natural history of the Puget Sound country. Seattle, WA:
University of Washington Press.
Kulkarni, M., Light, M., & Van Staden, J. (2011). Plant-derived smoke: Old technology with
possibilities for economic applications in agriculture and horticulture. South African
Journal of Botany, 77(4), 972-979.
Landis, T. D. (2000). Where there's smoke... There's Germination? Native Plants Journal, 1(1),
25-29.
Light, M., Daws, M., & Van Staden, J. (2009). Smoke-derived butenolide: Towards
understanding its biological effects. South African Journal of Botany, 75(1), 1-7.


 

54
 

Light, M. E., Burger, B. V., & Van Staden, J. (2005). Formation of a seed germination promoter
from carbohydrates and amino acids. Journal Agricultural Food Chemistry, 53(15),
5936-5942.
Light, M. E., Burger, B. V., Staerk, D., Kohout, L., & Van Staden, J. (2010). Butenolides from
plant-derived smoke: Natural plant-growth regulators with antagonistic actions on seed
germination. Journal Natural Products, 73(2), 267-269.
Lindon, H. L., & Menges, E. (2008). Effects of smoke on seed germination of twenty species of
fire-prone habitats in Florida. Castanea, 73(2), 106-110.
Lloyd, M. V., Dixon, K. W., & Sivasithamparam, K. (2000). Comparative effects of different
smoke treatments on germination of Australian native plants. Austral Ecology,25(6),
610-615.
Lonard, R. I., Judd, F. W., Smith, E. H., & Yang, C. (2004). Recovery of vegetation following a
wildfire in a Barrier Island grassland, Padre Island National Seashore, Texas. The
Southwestern Naturalist, 49(2), 173-188.
Luna, Tara; Evans, Jeff; Wick, Dale. 2008. Propagation protocol for production of Container
(plug) Elymus glaucus Buckl. plants 172 ml conetainers; USDI NPS - Glacier National
Park West Glacier, Montana. In: Native Plant Network. URL:
http://NativePlantNetwork.org (accessed 2016/05/01). US Department of Agriculture,
Forest Service, National Center for Reforestation, Nurseries, and Genetic Resources.
MacArthur, R. H., & Wilson, E. O. (1967). The theory of island biogeography. Princeton, NJ:
Princeton University Press.
MacDougall, A. S., & Turkington, R. (2007). Does the type of disturbance matter when restoring
disturbance-dependent grasslands? Restoration Ecology, 15(2), 263-272.


 

55
 

Nelson, D. C., Riseborough, J., Flematti, G. R., Stevens, J., Ghisalberti, E. L., Dixon, K. W., &
Smith, S. M. (2008). Karrikins discovered in smoke trigger Arabidopsis seed
germination by a mechanism requiring Gibberellic acid synthesis and light. Plant
Physiology, 149(2), 863-873.
Pennacchio, M., Jefferson, L. V., & Havens-Young, K. (2010). Uses and abuses of plant-derived
smoke: Its ethnobotany as hallucinogen, perfume, incense, and medicine. Oxford:
Oxford University Press.
Ranal, M. A., Santana, D. G., Ferreira, W. R., & Mendes-Rodrigues, C. (2009). Calculating
germination measurements and organizing spreadsheets. Revista Brasileira de
Botânica,32(4), 849-855.
Reyes, O., & Trabaud, L. (2008). Germination behaviour of 14 Mediterranean species in relation
to fire factors: smoke and heat. Plant Ecology, 202(1), 113-121.
Rook, E. J., Fischer, D. G., Seyferth, R. D., Kirsch, J. L., LeRoy, C. J., & Hamman, S. (2011).
Responses of prairie vegetation to fire, herbicide, and invasive species legacy. Northwest
Science, 85(2), 288-302.
Roy, B. A., Hudson, K., Visser, M., & Johnson, B. R. (2014). Grassland fires may favor native
over introduced plants by reducing pathogen loads. Ecology, 95(7), 1897-1906.
Schultz, C. B., Henry, E., Carleton, A., Hicks, T., Thomas, R., Potter, A., … Reader, B. (2011).
Conservation of prairie-Oak butterflies in Oregon, Washington, and British
Columbia.Northwest Science, 85(2), 361-388.
Seastedt, T. R. (1988). Mass, Nitrogen, and Phosphorus Dynamics in Foliage and Root Detritus
of Tallgrass Prairie. Ecology, 69(1), 59-65.


 

56
 

Soltani, E., Ghaderi-Far, F., Baskin, C. C., & Baskin, J. M. (2015). Problems with using mean
germination time to calculate rate of seed germination. Australian Journal of
Botany,63(8), 631.
Staden, J. V., Brown, N. A., Jger, A. K., & Johnson, T. A. (2000). Smoke as a germination
cue.Plant Species Biology, 15(2), 167-178.
Soós, V., Sebestyén, E., Posta, M., Kohout, L., Light, M. E., Van Staden, J., & Balázs, E. (2012).
Molecular aspects of the antagonistic interaction of smoke-derived butenolides on the
germination process of Grand Rapids lettuce ( Lactuca sativa ) achenes. New
Phytologist, 196(4), 1060-1073.
Thomas, P. B., Morris, E. C., Auld, T. D., & Haigh, A. M. (2009). The interaction of
temperature, water availability and fire cues regulates seed germination in a fire-prone
landscape. Oecologia, 162(2), 293-302.
Tilman, D. (1997). Community invasibility, recruitment limitation, and grassland
biodiversity.Ecology, 78(1), 81-90.
Tilman, D. (2004). Niche tradeoffs, neutrality, and community structure: A stochastic theory of
resource competition, invasion, and community assembly. Proceedings of the National
Academy of Sciences, 101(30), 10854-10861.
Tollefson, Jennifer E. 2006. Bromus carinatus. In: Fire Effects Information System, [Online].
U.S. Department of Agriculture, Forest Service, Rocky Mountain Research Station, Fire
Sciences Laboratory (Producer). Available: http://www.fs.fed.us/database/feis/ [2016,
May 4].
Turnbull, L. A., Crawley, M. J., & Rees, M. (2000). Are plant populations seed-limited? A
review of seed sowing experiments. Oikos, 88(2), 225-238.


 

57
 

Van Staden, J., Jäger, A., Light, M., Burger, B., Brown, N., & Thomas, T. (2004). Isolation of the
major germination cue from plant-derived smoke. South African Journal of Botany,70(4),
654-659.
Walsh, Roberta A. 1995. Dichanthelium acuminatum. In: Fire Effects Information System,
[Online]. U.S. Department of Agriculture, Forest Service, Rocky Mountain Research
Station, Fire Sciences Laboratory (Producer). Available:
http://www.fs.fed.us/database/feis/plants/graminoid/dicacu/all.html [2016, May 4].
Wicklow, D. T. (1977). Germination response in Emmenanthe Penduliflora
(Hydrophyllaceae).Ecology, 58(1), 201-205.
Winslow, Susan R.. 2002. Propagation protocol for production of Propagules (seeds, cuttings,
poles, etc.) Bromus carinatusseeds USDA NRCS - Bridger Plant Materials Center
Bridger, Montana. In: Native Plant Network. URL: http://NativePlantNetwork.org
(accessed 2016/05/01). US Department of Agriculture, Forest Service, National Center
for Reforestation, Nurseries, and Genetic Resources.
Wolf, A. (2001). Conservation of endemic plants in serpentine landscapes. Biological
Conservation, 100(1), 35-44.
Young, Betty. 2001. Propagation protocol for production of Container (plug) Danthonia
californica Boland plants San Francisco, California. In: Native Plant Network. URL:
http://NativePlantNetwork.org (accessed 2016/05/01). US Department of Agriculture,
Forest Service, National Center for Reforestation, Nurseries, and Genetic Resources.


 

58
 

Item sets

The Evergreen State College Masters Theses: Environmental Studies

Media

Ely_CMESThesis2016.pdf