Impacts of drought and bark beetles on red pine forests of the Anoka Plains, Minnesota
Executive Summary
Introduction
Objectives
Background
for Objective 1: Why regional differences?
Background
for Objective 2: Site-specific patterns in tree growth and mortality?
Background
for Objective 3: Are I. pini populations eruptive
on the Anoka Plains?
Methods
Objective
1: Regional comparison of precipitation, soils, river discharge, and tree growth
Objective
2: Site specific patterns in tree growth and mortality
Objective
3: Test for eruptive behavior in populations of Ips pini
Results and Discussion
Objective
1a: Regional comparison of precipitation and temperature
Objective
1b: Regional comparison of river discharge
Objective
1c: Regional comparison of soils
Objective
1d: Regional comparison of tree growth
Objective
2: Site specific patterns in soil moisture profiles, tree-growth, and tree mortality
Objective
3a: Abundance, species composition, and pheromone preferences of the bark beetle
community
Objective
3b: Test for eruptive behavior in populations of Ips pini
Conclusions
Regional
differences in tree growth, tree mortality, and beetle outbreaks
Application
of USGS hydrological discharge data
Correlations
within a region between local soil types, average tree growth, and stand susceptibility
to droughts
Implications
for understanding effects of climate on tree mortality and beetle populations
References cited
Executive
Summary
Red pine, the state tree of Minnesota, was an important
element of pre-settlement forests, and a significant timber species during the
early 20th century. Red pine has been widely propagated since the late 1950s
and has proven its value in terms of growth, pest resistance, soil conservation,
wildlife, biodiversity, aesthetics, recreation, and timber value. Also, it facilitates
a silvicultural system with regular selective harvests over a long rotation
time, which allows for growing economic returns to landowners and the forest
products industry while simultaneously favoring forested landscapes that include
more large trees and old-growth stands than the region has known since the early
1900s. Because it is only now that the first rotation of plantings are maturing
into forests, land managers have surprisingly limited experience on which to
base management decisions. For example, there is limited ability to know when,
or where, there will be consequential mortality of adult trees from drought
and bark beetles, and what, if anything, can be done to mitigate the undesirable
impacts. Motivated by the most recent drought, we conducted studies to address
the following questions: (1) Why is red pine mortality associated with drought
and bark beetles more common in the Anoka plains of east central Minnesota than
in nearby, apparently similar, forests; e.g., the Colfax region of west central
Wisconsin? (2) Are there predictable patterns in tree mortality within a region
that are related to soil type? (3) Do bark beetle infestations tend to become
self-perpetuating eruptions following a drought?
The Anoka Plains and
the Colfax region, separated by ~ 90 miles, both contain extensive red pine
forests that experience similar climates and grow on sandy soils derived from
glacial outwash. The Anoka Plains have received an average of 6% less annual
precipitation, which seems inadequate by itself to explain the history of recurrent
droughts and forest disturbance. However, analyses of river discharge data indicated
that the sandy soils of Anoka are different enough from the loamy sands of Colfax
to strongly affect the probability of droughts. In ~20 years since 1930, the
median weekly discharge rate from rivers that drain the Anoka plains have dropped
below 30% of the long-term average. This compares to only 1 year that rivers
draining the Colfax region have been so low. Droughts in 2000, 1988-89, 1976,
1964, and the 1930s were plainly evident in the river discharge data, which
suggests that real-time, online, discharge data provided by the USGS can be
used to recognize droughts at the time when tree water stress is maximal. The
recent drought at Anoka apparently reached its nadir in October of 2000. Some
tree deaths became evident the following winter. More extensive tree mortality
during the next two growing seasons was apparently due to an epidemic of the
bark beetle, Ips pini, that was triggered by the drought.
Regional differences in the rates of red pine growth and mortality are so large
that optimal silvicultural practices (e.g., harvest schedules) must be different,
but we know of no regionally customized guidelines that are presently available
to land owners and forest managers.
Results supported the
hypothesis that populations of I. pini are normally regulated
at endemic levels by resource limitations, but can switch to an epidemic state
following a resource pulse from drought-killed trees. Endemic populations of
I. pini may function chiefly as scavengers of trees that
are dying for other reasons, while epidemic populations seem to escape resource
limitations by attacking, killing, and reproducing within healthy trees. Under
this model, bark beetles amplify climatic effects into self-perpetuating episodes
of forest disturbance. Direct death of trees from drought may be less important
than drought as a factor that triggers state changes of bark beetles from endemic
to epidemic. Pest systems with multiple equilibria are ideal candidates for
cost-effective control, because occasional intervention can drive eruptions
back to endemic levels where they will tend to be maintained by natural regulatory
forces. In the case of I. pini, it is relatively cheap
and easy to monitor local populations with pheromone-baited funnel traps to
identify potential eruptions before they occur (our sampling suggested an action
threshold of ~ 500 I. pini / stand). To our knowledge,
this was the first test for eruptive population dynamics in I. pini.
Conclusions should be regarded as tentative, but indicate the possibility for
cost-effective mitigation of forest disturbance in regions such as the Anoka
Plains. We suggest that a plan be developed and implemented to evaluate different
possible strategies for pest monitoring and control. This could probably be
done in a way that: (1) permits validation or refinement of bark beetle population
models; (2) tests for possible undesirable side effects, e.g., removal of natural
controls by predators; and (3) provides immediate reductions in tree mortality
from beetles.
Introduction
At the time of European settlement, red pines (Pinus
resinosa) were a dominant element of forests throughout the
western Great Lakes region, especially in the sandy soils derived from glacial
outwash (Curtis 1959, Bonnicksen 2000). Red pine and white pine (P. strobus)
largely supported the early timber industry in this region (Walker 1998), which
in turn shaped the economic and cultural development of northern Minnesota and
Wisconsin (Fries 1951, Swanholm 1978, Birk 1999). Accordingly, red pine is the
state tree of Minnesota. Virtually all of the mature red and white pine forests
were logged by the 1930s and the associated forest products industry waned.
However, red pine has been widely propagated since the late 1950s and has proven
itself to be an excellent silvicultural option in that it: (1) grows well even
on sites that are barely arable without irrigation; (2) resists pests and pathogens
that often exert severe impacts on white pine stands (e.g., white pine weevils,
blister rust, and deer browsing); (3) contributes to soil conservation, protecting
the most vulnerable soil types from erosion by water (roots and duff layer)
and wind (year round foliage), often stabilizing sites previously eroded by
bad agricultural practices; (4) is a native species that generates wildlife
habitat and promotes biodiversity; (5) produces forests with broad human appeal
for aesthetics and recreation; (6) generates logs with good value and high demand;
and (7) facilitates a silvicultural system with regular selective cuttings but
a long rotation time, which allows for growing economic returns to landowners
and the forest products industry while simultaneously favoring forested landscapes
that includes more large trees and old-growth stands than the region has known
since the early 1900s.
Thus red pine forests
have returned to Minnesota and Wisconsin, and grow in size and value with each
year. As red pine regeneration programs of the 1950s and 1960s have begun producing
merchantable timber, red pine has already replaced depleted stocks of jack pine
and spruce to become the major source of softwood fiber for the Lake States
long established paper industry, and has re-energized the softwood lumber industry,
reversing a near century of decline. In Minnesota, red pine forests accounted
for 382 million acres in 2001 (compared to 71 million acres of white pine),
up from 247 million acres in 1977 (Minnesota Forest Resources Information Cooperative
2003). Similarly, a 1996 forest inventory in Wisconsin reported 988 million
cubic feet of red pine compared to 929 million cubic feet of white pine (Wisconsin
Department of Natural Resources 1996). The value of forest industry shipments
in WI during 1996 was $19.7 billion (compared to $8.4 billion in 1982). Furthermore,
the percentage of sawtimber volume in highest quality classifications (grades
1 and 2) increased from 28% in 1983 to 40% in 1996. As the size and value of
these forests grows, so grows the importance of their management.
Since it is only now
that the first rotation of plantings are maturing into 2nd growth forests, which
are destined to one day become our only old growth, foresters and landowners
have surprisingly limited experience on which to base some important management
decisions. For example, there is little basis for knowing when or where there
will be consequential mortality of adult trees from drought and bark beetles.
If some soil types or regions have predictably higher mortality rates for trees,
the expected half life for a cohort of trees will be reduced, which, among other
things, influences the successional trajectory of a forest managed for wildlife,
and changes the optimum harvest schedule of a forest managed for economic returns.
There is also little basis for evaluating the costs and benefits of pest control
efforts in mature stands of red pine. One of the most significant pests of mature
pines in the Great Lakes region is the pine engraver beetle, Ips pini (Schenk
and Benjamin 1969, Sartwell et al. 1971, Geiszler et al. 1984, Klepzig et al.
1991, Rasmussen et al. 1996, Kegley et al. 1997, Ayres et al. 1999, Santoro
et al. 2001). I. pini is regarded by many forest entomologists
as an occasionally eruptive species (Berryman 1987) that normally has little
impact on healthy trees, but which can produce sustained outbreaks when environmental
conditions such as a drought or windthrow allow the development of large populations
that then become self-sustaining through continued successful mass-attacks on
otherwise healthy trees. Such populations are excellent candidates for cost-effective
control because occasional efforts can suppress eruptions back to low (endemic)
populations levels where they then tend to be regulated by natural forces. Based
on this theoretical principle, rather extensive control programs (mass-trapping)
were conducted in the Sand Dunes State Forest following the drought of 1988-89
and in Itasca State Park following the windstorms of 1996-97. However, the underlying
theory has not been tested for I. pini. If it does not
hold, then bark beetle control efforts such as mass-trapping or sanitation logging
would have less benefit, no benefit, or even make matters worse by delaying
the onset of natural controls from predators.
Objectives
We conducted studies during 2002 to address the following
questions:
1. Why is tree mortality associated with bark
beetles more common in the Anoka plains than in superficially similar regions,
e.g., west central Wisconsin?
2. Are there predictable patterns in tree
mortality within a region that are related to soil type?
3. Do bark beetle infestations tend to become
self-perpetuating eruptions following a drought?
Background
for Objective 1: Why regional differences?
The Anoka Plains of east central Minnesota, including Sand Dunes State Forest
in Sherburne Co., contains significant stands of red pine that generally grow
well but have a history of bark beetle outbreaks coincident with droughts (e.g.,
1976, 1988-89, and 2000-01). The Colfax region of nearby west central Wisconsin
also contains extensive stands of red pine that are comparable in age and structure
to those in MN. However, tree mortality from bark beetles or drought is very
rare in the Colfax region. In 15 years of studying bark beetles in red pine
forests, we have only witnessed very occasional instances of individual trees
that might have died from drought or bark beetles, and we have never observed
the simultaneous infestation of multiple live trees. Most foresters and landowners
in the Colfax region understandably ignore bark beetles in their management.
These two regions have similar sandy soils derived in part or whole from glacial
outwash and are near enough (90 miles) that one would expect similar temperatures
and precipitation (Fig. 3). We compared these regions
with respect to historical patterns in precipitation to test whether climatic
patterns could account for the apparent differences in tree mortality from droughts
and bark beetles. We also compared soil characteristics and river discharge
patterns to test the alternative hypothesis that patterns are due to soils and
drainage rather than climate. Finally, we compared regions with respect to site
index for red pines and interannual variation in diameter growth to test whether
trees on the Anoka Plains are more water limited for any reason.
Background
for Objective 2: Site-specific patterns in tree growth and mortality?
Sites that are generally suitable for red pine in the Anoka Plains include some
soils with banding, which tends to slow the drainage of soil water out of the
rooting zone, and other soils that lack banding. Soils with banding appear to
support higher tree growth on average, presumably because of increased access
to water, but may also increase susceptibility to drought. This could be because
root systems on banded soils are shallower, due to generally higher water availability
in the upper soil zones and increased mortality of those roots that extend into
deeper zones subject to water saturation that limits oxygen supply. Trees with
such root systems may be more susceptible to drought during dry years when water
becomes depleted in the upper soil zones. Thus, red pines growing on soils with
low site index (reflecting average growth) may develop deeper root systems that
make them better able to survive droughts. One alternative hypothesis is that
average growth is positively correlated with drought tolerance, including resistance
to bark beetles. We tested these hypotheses by measuring tree growth, and tree
mortality associated with a recent drought, across a range of soil types near
Sand Dunes State Forest in MN. We also measured soil water profiles within each
site.
Background
for Objective 3: Are I. pini populations
eruptive on the Anoka Plains?
During July 2001, more than 50 patches of red pine mortality were detected
in Sherburne and Isanti Counties during aerial surveys by Minnesota Forest Health
personnel. This was thought to be the result of a drought during 2000, which
had ended by 2002. The eruption hypothesis assumes that populations are regulated
around one of two equilibria, at endemic or epidemic levels (Fig.
1). Under this model, populations can undergo a state change from endemic
to epidemic if some exogenous factor (e.g., a drought that kills some trees
and produces a pulse of high quality food resources) permits populations to
exceed an escape threshold beyond which further resource limitations are relaxed
because they are able to employ mass-attacks to kill additional trees. In the
case of bark beetles, resource limitations that regulate populations around
the endemic equilibrium are expected to produce a pattern of increasing colonization
density in suitable host material (fresh logs and recently killed trees) with
increasing abundance of colonizing adults within the forest stand. When local
abundance of colonizing adults exceed the hypothetical escape threshold, colonization
density in logs is predicted to decline as some adults participate in attacks
of nearby live trees. We tested these predictions (Fig. 2)
with studies of multiple infestations in and around the Sand Dunes State Forest,
a putative epidemic population, and multiple stands of red pine on the Colfax
Plains, a putative endemic population.
Methods
Objective
1: Regional comparison of precipitation, soils, river discharge, and tree growth
We identified 10 weather stations within about 50 km of our study sites
near Anoka, MN (Fig. 5) and Colfax, WI (Fig.
6). Monthly climate records since 1940 were downloaded for each site from
the National Oceanic and Atmospheric Association (NOAA 2003). We calculated
annual growing season precipitation for each site as the total from 1 October
of the previous year through 30 September of the growing year. We calculated
indices of summer and winter temperatures as average daily temperate for June-August
and December-February, respectively.
We identified two United
States Geological Service gaging stations in each region with on-line, long
term records of daily discharge rates: Elk River near Big Lake, MN (USGS 2003a),
Rum River near St. Francis, MN (USGS 2003b), Red Cedar River at Menomonie, WI
(USGS 2003c), Hay River at Wheeler, WI (USGS 2003d). The location of these gaging
stations is indicated on Figs. 5-6, and, in higher resolution, at the USGS web
sites in the bibliography. We downloaded the full history of daily discharge
rates for each station, which went back to 1930 in most cases. Daily discharge
rates showed frequent brief surges that corresponded to precipitation events,
but also indicated a tendency to return towards a moving baseline that reflects
the rate of groundwater input and might be interpretable as a measure of regional
soil water availability for trees. We estimated this moving baseline for each
station for each week of the data record (as the median of 7 daily records).
The weekly interval was selected as being a time period that is physiologically
relevant to trees; i.e., a week of severe water deficits would be expected to
evoke drought stress in trees. To look for drought signals over the full 70
year record, we calculated the annual minimum of median weekly discharge for
each station and plotted the time series and frequency distributions. These
data were compared against historical reports of droughts in both regions. Weekly
discharge rates were plotted for 3-4 year intervals that encompassed putative
droughts at Anoka. We also plotted the frequency distributions of median weekly
discharge rates (n ~ 3600 weekly values for each site).
We used USDA soil
surveys for Sherburne County, MN and Dunn County, WI to compare the attributes
of the soils supporting the red pine stands that we studied. We calculated site
indices for red pine at a sample of 30-50 year-old red pine stands in each region
(see below). We extracted increment bores from red pines in both regions, including
a sample of 60-100 year-old trees, to test for regional differences in the effects
of water availability on annual diameter growth.
Objective
2: Site specific patterns in tree growth and mortality
We selected 8 red pine stands near Sand Dunes State Forest to include
a spectrum of soil types and a range of tree mortality following the drought
of 2000 (Fig. 4). We also chose 5 sites near Colfax,
WI (separated by 1 - 10 km) that included a spectrum of soil types in this region.
At each site, we measured tree heights with a laser hypsometer, diameter at
breast height of 5 trees / site, and basal area with an English BAF 10 prism
(3 measurements / site). We extracted and mounted increment cores at 1 m height
from 3 trees at each site. Site index was calculated from age and height following
Lundgren and Dolid (1970). On 23-27 August, 2002, we collected one soil core
from each site (3/4" diameter to 90 cm depth). Cores were sectioned into 14
cm lengths, weighed immediately, then dried and re-weighed to obtain water content
as percent mass. At the same time, we surveyed 600-1000 trees at each site to
estimate percent mortality during 2000, 2001, and 2002. Trees with no needles
produced during the last year, and few dead needles still remaining on the tree,
were judged to have died during 2000. Those with no live foliage, but holding
needles produced during 2001 were judged to have died during 2001, and those
with red foliage and current beetle attacks were classified as dead in 2002.
These categories seemed to be quite discrete.
Objective
3: Test for eruptive behavior in populations of Ips pini
We used 12-unit Lindgren funnel traps to estimate the abundance of
Ips bark beetles at each study site during the early summer
flight period in 2002 (4 weeks of sampling from 26 May to 25 June). This sampling
was timed to capture beetles that had successfully overwintered and were destined
to reproduce during the summer. At each site, we deployed an array of four funnel
traps, configured as an approximate square of ~ 20 x 20 m. Two traps per site
were baited with the pheromone signal of Ips pini, ipsdienol
+ Lanierone, one was baited with the pheromone signal of I. grandicollis,
ipsenol, and one was baited with the pheromone signal of I. perroti,
ipsenol and ipsdienol (Ayres et al. 2001). Pheromone lures were bubblecaps purchased
from PheroTech: elution rates of 0.2 mg / d for ipsdienol (racemic) and ipsenol,
and 0.01 mg / d for Lanierone. Traps were emptied weekly and, at the same time,
lures were rotated among traps to guard against spurious effects from trap position.
Later, trap captures were counted and identified.
At each site, we also
measured beetle colonization densities in logs. In late May, two trees were
felled at each site, and 5, 50-cm long logs were removed from the mid-bole of
each tree. At this time, 5 logs (2 or 3 from each source tree) were spread over
each site (one log near each funnel trap, and one in the center of the trapping
area). The other five logs were covered with a tarp, to prevent beetle colonization,
until 15-20 July, when they were placed in the same locations as the first set
of logs to provide a resource for colonization by the 2nd generation
of I. pini. At this time, the first set of logs were consolidated
and covered with a tarp to prevent further colonization by beetles. On 22-27
August, we measured the colonization density by Ips of
each trap log. We carefully removed a 40 x 22 cm section of bark from the upper
surface of each log and counted the number of oviposition galleries, each representing
one adult female that entered the log and began laying eggs. For each site,
we calculated average experienced attack density, ExpAD,
as:
Eq 1
where I = index for each log within a site, imax = the number of logs within a site, nI = number of attacking females per log, and areaI = dm2 of area sampled within each log. This calculates the density experienced by an average ovipositing female within each site, which is more appropriate than the average density per log for estimating effects of intraspecific competition on population growth rate. It turned out that by the time of our measurements in late August, the logs colonized during June were too damaged by wood borers and other phloem-feeding insects to measure Ips colonization densities. Hence, our subsequent analyses were restricted to logs colonized after 15 July. When we examined the logs in late August, we collected samples of adult Ips from the trap logs for identification. Not all of these have been examined yet, but it appeared that most, or all, were I. pini, which is as expected since the I. pini always has multiple generations per year in this region, while I. grandicollis and I. perroti typically just have a single generation (Ayres et al. 2001).Results
and Discussion
Objective
1a: Regional comparison of precipitation and temperature
Since 1940, annual precipitation near Anoka averaged about 6% less, with
slightly greater inter-annual variation, than near Colfax: average mean + average
SD = 29.5 + 6.3 inches / year vs 31.9 + 5.5 inches / year (Table
1). Average summer temperatures were slightly warmer near Anoka (68.7 vs.
67.7 °F) and average winter temperatures were slightly cooler (14.5 vs. 15.3
°F; Table 1). Neither Table 1 nor Fig. 7 indicated that
the Anoka sand plains near Sand Dunes State Forest receive less precipitation
than areas 20-30 miles further north, south, east, or west. Stations at Santiago
and Elk River, about 10 miles north and south, respectively, of Sand Dunes State
Forest (Fig. 5), have received annual precipitation that is representative for
the broader area (Table 1), Fig. 7). In general, there was little variation
in annual precipitation among sites within a region. The time series of annual
precipitation since 1930 showed clear inter-annual variation in both regions,
and some of the historical droughts were evident in the Anoka time series (Fig.
7); e.g., precipitation lows during 1976, 1987-88, and 2000 correspond to times
of drought as evidenced by tree mortality and, sometimes, peat fires. Droughts
reported in 1980-81 and 1965 were less evident in the Anoka precipitation data,
and the extended drought of the mid 1930s (“Dust Bowl”) was not
very conspicuous. The precipitation time series for Colfax (Fig. 7, lower) was
qualitatively similar to that of Anoka. In Fig. 7, there appear to be fewer
years at Colfax vs. Anoka that stand out as having conspicuously lower precipitation.
On the other hand, comparison of frequency distributions (Fig.
8) indicate that the interannual variation in precipitation was quite similar
between regions. In general, interannual precipitation patterns were well correlated
between the regions; i.e., dry years in Anoka also tended to be dry years in
Colfax (Fig. 9).
Objective
1b: Regional comparison of river discharge
River discharge data showed very clear signals of all the reported droughts
near Anoka (Fig. 10). Interannual variation in minimum
weekly discharge rates were highly correlated between Rum River and Elk River,
indicating that minimum weekly discharge is primarily driven by regional climatic
patterns, rather than local land use, or local precipitation events. In both
watersheds, an empirical drought threshold of < 30% of the long term average
in weekly discharge rates did a good job of identifying drought years - better
than precipitation patterns (compare Fig. 10 and Fig. 7).
Discharge data from two rivers near Colfax area also showed high correlation
across years (Fig. 11). The dry years of 1988-89 and
the Dust Bowl were evident in the Colfax rivers, but, in contrast to the Anoka
Plains, the annual minimum in weekly discharge rates never dropped below 30%
of the long term average. This is consistent with the historical rarity of tree
mortality from drought in the Colfax region. The frequency distributions of
minimum annual discharge from the Anoka Plains differed from those of the Colfax
region in tending to be skewed to the left (Fig. 12);
i.e., a larger proportion of the years had low minium discharge rates in the
Anoka Plains than near Colfax. The regional differences were even more pronounced
in the frequency distributions of weekly discharge rates (Fig.
13). The variance in weekly discharge was dramatically higher in the Anoka
Plains than near Colfax: coefficient of variation (SD / mean) = 1.23 and 1.31
for Elk and Rum Rivers vs. 0.67 and 0.83 for Red Cedar and Hay Rivers. Thus,
weekly discharge in the Anoka Plains frequently dropped below the empirical
drought threshold of 30% of the average while this has almost never happened
in the Colfax region (Fig. 13). Note that there were strong regional differences
in discharge variability even though precipitation variability was quite similar
(compare Figs. 8 and 13).
Discharge data also permitted
higher resolution in identifying the timing of historical droughts (Fig.
14). For example, discharge data indicate that the recent drought reached
its nadir in October-November of 2000 (Fig. 14, upper), which is consistent
with observations of dead and dying trees during aerial surveys in the winter
of 2000-2001. Discharge rates remained above the drought threshold during 2001
and were well above average during 2002. Discharge data indicate that the drought
of the late 1980s extended through two summers, 1988-89, and followed record
highs during the summer of 1986 (Fig. 14, 2nd panel), which might have exacerbated
the effects by producing root mortality in saturated soils. The drought of 1976
reached its nadir in September of 1976 (Fig. 14, 3rd panel), and the drought
reported from the mid 1960s appears to have reached its nadir in August of 1964
(Fig. 14, lower panel).
Objective
1c: Regional comparison of soils
Our study sites
spanned four mapped soil types within each region (Table
2). Both regions include sandy soils, derived from glacial outwash, that
are characterized as having excessive permeability, limited available water
capacity, and low fertility. However, the pine-bearing soils of the Anoka Plains
are almost exclusively glacial outwash while the Colfax region also includes
sandstone residuum derived from the sandstone that was only 30-60 cm below the
surface of two study sites. There are two separate glacial histories in the
Colfax lobe of the Central Plain in Wisconsin. The entire landscape was thought
to be glaciated only once, covered by the farthest reach of the first Wisconsinian
glacial advance, the Altonian (30,000-50,000 YBP). It was very thin in the Colfax
area, and thirty thousand years later, the till left behind is only inches deep
on the upland areas that were not covered and reshuffled by the outwash of a
later glacial advance, the Woodfordian (ca 10,000 YBP), which stopped ~ 30 km
north of our study sites (Paull and Paull 1977). Now the region includes numerous
sandstone ridges (20-60 m high) covered by shallow soils (18-60 cm ) made up
of weathered Altonian residuum, plus loess and decayed sandstone. The soils
between the ridges, especially near rivers that drained the Northern Highlands,
contains extensive sandy glacial outwash of the Woodfordian glacier (Laberge
1994). Thus, soils of the Colfax region, although tending to be sandy throughout,
have two different histories, and somewhat different characteristics: tending
to be relatively deep, outwash sands in the lowlands, versus shallow loams,
underlain by sandstone, on the ridges. The two soils commingle and intergrade
throughout the region..
The Anoka soils are classified
as fine sand, loamy fine sand, or fine sandy loam. While the Colfax soils are
loamy sand or loam. This suggests larger particle size and more rapid drainage
through the Anoka soils compared to Colfax, which is consistent with the pattern
of more variable river discharge rates from Anoka (Fig.
12), and more frequent drought (Figs. 10 vs. 11), even though precipitation
is only 6% lower and no more variable (Fig. 8). Based
on the soil survey data, the regions also differ in that Anoka soils tend to
be more acidic and have lower available water capacity (Table
2). Somewhat surprisingly, the soil survey data revealed no differences
in permeability or percentage of soil passing through sieves of four different
size classes..
Objective
1d: Regional comparison of tree growth
The regional differences in red pine growth were larger than we guessed
a priori. In Anoka, stands that were 45 - 55 years old
were 52 - 66 feet tall and 7.7 - 10.9 inches diameter, while in Colfax, the
stands were 4 - 15 years younger, but the trees were larger: 67 - 72 feet tall
and 8.6 - 11.0 inches in diameter (Table
3). We calculated the average site
indices (expected height at 50 years) to be 60 vs 84 feet at Anoka vs. Colfax.
By comparison, site indices calculated for similarly aged red pine stands near
Itasca State Park in western MN averaged 58 ft (Ayres et al. 1999).
We have not yet completed
analyses of historical growth patterns based on tree rings, but visual inspection
of the cores suggests that diameter growth on the Anoka Plains was somewhat
lower on average, and much more variable between years, than in the Colfax region.
We hypothesize that climatic effects on red pine growth will be weak or absent
near Colfax, but strong, and related to droughts as quantified by river discharge,
near Anoka.
Objective
2: Site specific patterns in soil moisture profiles, tree-growth, and tree mortality
Tree mortality associated with the 2000 drought on the Anoka Plains ranged
from 6 to 122 trees / 1000 (Table 3). There was no
obvious association between site-specific tree growth and tree mortality. Anoka
sites with the highest tree mortality (4 and 6) had the lowest and highest site
indices (Table 3). Neither were there clear associations between mapped soil
types and tree growth or tree mortality (Table 3). Soil type 1258 fs included
one site with low growth and high mortality and another with high growth and
low mortality. Three sites on soil type 158A fs also included a broad range
of site indices and tree mortality. Two sites on soil 1256 lfs had low site
indices and moderate tree mortality. Further tests will be possible after the
analysis of growth rings. The original hypothesis predicts that sites with the
highest average growth tend to have high interannual variance in growth, and
relatively high rates of tree mortality. Ideally, tests for relationships between
tree growth, soil, and tree mortality would begin by selecting study sites at
random with respect with tree mortality, which was not the case here (because
tests for eruptive population dynamics - Objective 3 - were stronger with sites
deliberately chosen to span a range of beetle abundance and tree mortality)).
Soil moisture profiles
showed evidence of perched water in some sites at Anoka but not others (Fig.
15). In 7 of 8 sites at Anoka, soil moisture at most depths, at the time
of our sampling was about 5% by mass. In site 2, soil moisture increased from
5% at 60 cm to 12% at 85 cm. In site 5, soil moisture was elevated to near 10%
at 18 cm, and to 17% at 78 cm. The fine sandy loam at site 10 had substantially
higher water content, averaging about 10%, with higher amounts in the upper
10 cm, and declining amounts below 70 cm (Fig. 15). The sites that showed evidence
of perched water (2, 5, and 10) had site indices that were average or below
average (56, 61, and 53 ft; Table 3). Soil moisture
profiles varied somewhat within mapped soil types (Fig. 15). Inferences from
the soil moisture measurements are constrained because we had no replication
within sites or across dates. Thus we cannot judge whether measurements are
representative for the stands, even on the day of measurements. However, it
appears that more such sampling would be feasible and permit a rigorous test
of the hypothesis that red pines growing in banded soils tend to have higher
growth on average, but are also more susceptibility to drought.
Soil moisture in the
two loamy sands at Colfax also tended to be about 5% (Fig.
16). Chamnis North showed evidence of some perched water at about 50 cm
and 85 cm. At Dickinson, soil water jumped to > 10% near 62 cm depth. The
two loam soils, which lay only 30 60 cm above sandstone, had conspicuously higher
soil moisture of ~ 10%. Calculated site indices were very constant among 4 sites
(80 - 84 ft) and somewhat higher (89 ft) on one of the sites with PdB loamy
sand.
Objective
3a: Abundance, species composition, and pheromone preferences of the bark beetle
community
As expected, I. pini were more abundant in the Anoka
Plains compared to the Colfax region (Table 4). With
the same trapping protocol, captures of I. pini from late
May to late June (the flight time of the overwintering generation) averaged
about 8-fold higher in Anoka vs. Colfax (826 / site vs. 111 / site; Table 4).
I. grandicollis were also more abundant in Anoka, but less
so (only about 50% higher). Surprisingly, I. perroti were
actually less abundant in Anoka than Colfax (Table 4). The two most abundant
predators, Thanasimus dubius (Coleoptera: Cleridae) and
Playtsoma cylindrica (Coleoptera: Histeridae) were both
about 7-fold more abundant in Anoka than Colfax. The abundance of predators
relative to prey, (T. dubius + P. cylindrica)
/ total Ips, was about 2.5x higher in Anoka compared to
Colfax. This is consistent with the hypothesis that these specialist predators
increase in their abundance after a year or two of high prey abundance. Presumably,
this generates some negative feedback (with a delay) on the population growth
rates of bark beetles (as has been reported for some other bark beetle systems;
Turchin et al. 1999). It is not known whether or not this negative feedback
is sufficient to eventually drive bark beetle populations back to an endemic
equilibrium, or whether it is merely sufficient to regulate abundance around
an epidemic equilibrium (see Fig. 1)
Bark beetle pheromone
preferences in both regions matched those reported in earlier studies conducted
near Colfax, WI and Itasca State Park, MN (Table 5):
95 -96% of I. pini were captured in traps baited with ipsdienol
+ Lanierone; and 73 - 94% of I. grandicollis were captured
in traps baited with ipsenol by itself. The two most abundant predators were
captured with all three pheromone signals, but were most attracted to the signal
that is produced and preferred by I. perroti (ipsenol + ipsdienol). This
suggests a hypothesis for why I. perroti were relatively rare in the
forests where I. pini were very abundant.
Objective
3b: Test for eruptive behavior in populations of Ips pini
As expected, beetle-attacked trees were common in the Anoka Plains
and very rare in the Colfax region: average tree mortality rates during the
three years from 2000-2002 were 15.8 vs. 0.5 tree deaths per 1000 trees per
year for Anoka and Colfax, respectively (Table 3).
Across 8 red pine stands on the Anoka Plains, average tree deaths per 1000 were
6.4 in 2000, 24.7 in 2001, and 6.9 in 2002. In all but one Anoka site, tree
deaths peaked in 2001. Tree attacks during 2002 were positively related to abundance
of I. pini during early summer (Fig.
17, upper). There was a suggestion of a threshold for tree attacks, as predicted
by the theoretical model for eruptive population dynamics (Fig.
2, upper). Tree attacks became relatively common when early summer trap
captures of I. pini exceeded about 500 per two traps per
month (Fig. 17, upper).
Colonization densities
of logs by I. pini were also higher in Anoka than Colfax:
mean experienced density + SE = 2.5 + 0.1 vs. 1.1 + 0.2 ovipositing females
/ dm2, respectively (Table 2).
Across all 13 red pine stands that were studied, the density of I. pini
in logs colonized during August was related to trap captures of overwintering
I. pini adults during June (Table 2). However, this relationship
was nonlinear, with a peak when trap captures were intermediate (Fig.
17, lower). There was strong statistical support for the nonlinearity of
this relationships (AIC for 2nd order polynomial vs. linear model = 5.57). The
form of this relationship, and the match between a threshold for tree attacks
and the peak in colonization density, were as predicted by the theoretical model
for eruptive population dynamics (compare Figs. 2 and 17). The support for this
model, although based on only a single year of data, is strengthened by the
fact that the test involved rather specific predictions about the interrelations
among three independent variables (local abundance as measured by trap captures,
colonization densities in logs, and the number of live trees attacked during
the summer). Presumably, beetle colonization densities in logs started to decline
after trap captures exceeded about 800 because some beetles were participating
in successful attacks of live trees, which increased the resource base for ovipositing
females, and eased competition for phloem. Results suggest that the escape threshold
for I. pini (Nescape in Fig.
1) is at 600 - 800 captures per two funnel traps per month.
Conclusions
Regional
differences in tree growth, tree mortality, and beetle outbreaks
Tree mortality rates are clearly much higher on the Anoka Plains than
areas within 90 miles that experience similar climates and have similar sandy
soils. This was obvious not only from the counts of mortality events during
the last 3 years, but also from dramatic differences between the regions in
the numbers of downed trees from earlier deaths; such logs were abundant throughout
pine stands in the Anoka Plains but were rare or absent in pine stands near
Colfax. The differences in tree mortality are difficult to explain based on
the modest (6%) difference in average annual precipitation. Apparently there
is a strong effect from the Anoka Plains being made up of soils that drain more
rapidly than those near Colfax. Still, the direct effects on red pine forests
of lower and more variable soil water would probably be modest were it not for
the presence of bark beetles that can apparently be triggered by drought episodes
to switch from endemic populations that rarely kill trees to epidemic populations
that commonly kill trees. Thus the explanation for differences between red pine
forests near Anoka and Colfax appear to involve strong interactions between
climate, soils, and beetle population dynamics. The regional difference in tree
mortality rates is surely enough to influence optimal harvest schedules, and
is also surely enough to warrant careful consideration of bark beetle management
on the Anoka Plains, even while forest managers near Colfax can generally ignore
them without consequence.
With constant annual
mortality rates of 0.5 / 1000, such as we observed at Colfax, and other things
being equal, a red pine stand would experience 48 deaths / 1000 trees over 100
years. Since 1930, there appear to have been about six significant droughts
on the Anoka Plains. We estimated that the 2001 drought resulted in mortality
of 15.8 trees / 1000. If there is one drought per 12 years that results in the
death of 15.8 trees / 1000, on top of a background annual mortality rate of
0.5 / 1000, a red pine stand would experience 175 deaths / 1000 trees over 100
years. These calculations are very simplistic. In particular, they fail to account
for: (1) the risks of catastrophic losses associated with droughts more severe
than that of 2001; (2) mortality risks associated with fire, blowdown, fungal
pathogens, and ice damage; (3) potential for minimizing risks through selective
harvesting. Nonetheless, these calculations suggest that there would be value
in developing more sophisticated projections to aid in the development of long
term management plans for red pine stands that account for regional differences
in tree growth and mortality rates on timber yield and stand structure over
50 - 100 year time frames. Our sense is that it is realistic to manage red pine
stands near Colfax for a time frame of >100 years, while reasonable rotation
times for red pine stands near Anoka may be substantially less. These calculations
also suggest that the expected lifespan for red pine stands near Anoka may be
extremely sensitive to consideration of bark beetle risks in site selection
and management.
In addition to modifying
red pine management strategies on the Anoka plains, it may make sense to consider
other tree species for future reforestation. Because tree/bark beetle interactions
can be quite species-specific, and because tree species differ in moisture requirements
and drought response, planting other conifers instead of red pine, may make
sense. Mixed species plantings in some areas have shown promise for managing
pest/tree interactions, and offer the additional benefit of providing a more
diverse ecosystem. Our work offers no insight as to the suitability of alternate
tree species, but could help establish parameters for comparisons.
Application
of USGS hydrological discharge data
Analyses of river discharge data suggest that there would be value in
monitoring USGS discharge data to recognize potential droughts in the early
stages and implement appropriate, cost-effective responses (e.g., minimizing
log decks that could permit buildups of bark beetles, and conducting aerial
and ground surveys for early signs of tree deaths and beetle activity). This
would also facilitate studies of tree water status and resin defenses during
the time of presumed maximal water deficits. Such studies are needed to understand
how drought influences the defenses of trees that would survive in the absence
of beetles. Available data suggest that resin defenses of pines are actually
increased by moderate water deficits (Reeve et al. 1995, Ayres et al. 1999,
Lombardero et al. 2000), but patterns at Anoka are also consistent with the
alternative hypothesis that drought stress compromises tree defenses. Resolution
of these competing hypotheses will aid in understanding how beetle control efforts
and stand management can mitigate risks of tree mortality.
USGS
river discharge data may have broader applicability for: (1) objectively identifying
regions that are generally susceptible to consequential droughts; and (2) monitoring
entire states for local or regional droughts. This broader applicability depends
upon the unvalidated proposition that patterns identified here based on four
rivers in two county-sized regions can be extended to a broader spatial scale.
However, it would cheap and easy to begin evaluating the generality of, for
example, the 30% drought threshold suggested here. Among other benefits, results
would likely enhance our ability to anticipate the consequences for forests
of changes in temperature and precipitation that have already occurred and are
likely to accelerate (U.S. Global Change Research Program 2000). We can expect
climate changes to continue to alter patterns of soil water availability in
Minnesota, and the effects on forests, whether positive or negative, are likely
to be the largest and most immediate in regions like the Anoka. Plains.
Correlations
within a region between local soil types, average tree growth, and stand susceptibility
to droughts
We were unable to resolve what, if any, are the patterns between local
soil types, tree growth, and stand susceptibility to drought and beetles. However,
the question is important and deserves further study. We suggest that a subsequent
study include replicate pine stands selected at random from within different
mapped soil types. Within these stands, one could measure: (1) soil moisture
profiles as in Figs. 15-16, replicated within each stand and across the season;
(2) tree mortality via surveys for dead trees and downed logs; (3) historical
patterns in height and diameter growth; and (4) depth of roots. Results would
aid forest managers and landowners in selecting sites for red pine propagation,
and customizing management of red pine stands for site-specific characters (e.g.,
harvesting schedules, tree selection during harvesting, pest monitoring, and
pest control).
Implications
for understanding effects of climate on tree mortality and beetle populations
Results indicate that there are potential benefits to monitoring populations
and treating those that have exceeded the escape threshold that separates endemic
populations from eruptions. Apparently, climate and beetles interact to determine
tree mortality rates and forest disturbance regimes. Direct death of trees from
drought may be less important than drought as a factor that triggers state changes
of bark beetles from endemic to epidemic. If it were otherwise, the impacts
of beetles would be restricted to times when trees are dying, or have compromised
defenses, as a result of climatic stress. As it appears to be, beetle mortality
may continue for years after a drought abates. Potential control strategies
for Ips in red pine forests include mass-trapping with pheromone-baited
funnel traps, deployment and destruction of trap logs, and aggressive sanitation.
In our judgement, it remains to be established that these control strategies
can be effective and practical for pine systems in Minnesota, but if I.
pini populations tend to have endemic and epidemic states (Fig.
1), there is potential value in pest control. The correlation among stands
between trap captures in early summer and tree attacks during the summer, suggests
that control might be effective at the stand level (not necessarily requiring
expensive regional efforts). We recommend that a plan be devised for implementing
pest control efforts in some stands that are above the estimated escape threshold
(Fig. 17) and leaving other such stands as controls.
This would permit the evaluation of different possible control strategies, the
continued testing and refinement of models to predict bark beetle population
dynamics, careful assessment of possible undesirable side effects (e.g., removal
of natural controls by predators) and, hopefully, the mitigation of expensive
beetle impacts within treated stands.
Ayres, B. D., M. P. Ayres, M. D. Abrahamson, and S. A. Teale. 2001. Resource partitioning and overlap in three sympatric species of Ips bark beetles (Coleoptera : Scolytidae). Oecologia 128:443-453. weblink
Ayres, M. P., M. J. Lombardero, B. D. Ayres, and A. E. Santoro. 1999. The biology and management of bark beetles in old growth forests of the Itasca State Park. Great Lakes Institute of Pine Ecoystem Research, Colfax, WI. weblink
Berryman, A. A. 1987. The theory and classification of outbreaks. Pages 3-30 in Barbosa, P. and J. C. Schultz, editors. Insect outbreaks. Academic Press, New York.
Birk, D. A. 1999. Outta the Woods and Onto the Mills: Shifting Timber-Harvest Strategies on Minnesota's Early Lumbering Frontiers. Institute for Minnesota Archeology. http://www.fromsitetostory.org/sources/papers/mnlogging/mnlogging.asp
Bonnicksen, T. M. 2000. America's ancient forests. John Wiley and Sons, New York.
Curtis, J. T. 1959. The vegetation of Wisconsin. University of Wisconsin Press, Madison, Wisconsin.
Fries, R. F. 1951. Empire in Pine: The Story of Lumbering in Wisconsin, 1830-1900. State Historical Society of Wisconsin, Madison, WI. 285 pp.
Geiszler, D. R., R. I. Gara, and W. R. Littke. 1984. Bark beetle infestations of lodgepole pine Pinus contorta var murrayana following a fire in south central Oregon USA. Zeitschrift Fuer Angewandte Entomologie 98:389-394.
Kegley, S. J., R. L. Livingston, and K. E. Gibson. 1997. Pine engraver, Ips pini (Say) in the western United States. Forest Insect and Disease Leaflet 122. USDA Forest Service, Washington, D.C.
Klepzig, K. D., K. F. Raffa, and E. B. Smalley. 1991. Association of a insect-fungal complex with red pine decline in Wisconsin. Forest Science. 37:1119-1139.
Laberge, G.L. 1994. Geology of the Lake Superior Region. Geoscience Press Inc., Phoenix, Arizona. pp 269-273
Lombardero, M. J., M. P. Ayres, P. L. Lorio, Jr., and J. J. Ruel. 2000. Environmental effects on constitutive and inducible resin defences of Pinus taeda. Ecology Letters 3:329-339. weblink
Lundgren, A. L. and Dolid, W. A. 1970. Biological growth functions describe published site index curve for Lake States timber species. - USDA Forest Service North Central Forest Experiment Station Research Paper NC-36: 1-9
Minnesota Forest Resources Information Cooperative. 2003. http://www.cnr.umn.edu/FR/research/centcoop/mfric/data.htm
NOAA. 2003. Locate weather observation station record. http://lwf.ncdc.noaa.gov/oa/climate/stationlocator.html
Paull, R.K. and R.A. Paull. 1977. Geology of Wisconsin and Upper Michigan. Kendall/Hunt Publishing Co., Dubuque, Iowa. pp 97-105
Rasmussen, L. A., G. D. Amman, J. C. Vandygriff, R. D. Oakes, A. S. Munson, and K. E. Gibson. 1996. Bark beetle and wood borer infestation in the greater Yellowstone area during four postfire years. USDA Forest Service Research Paper INT-RP-487:1-10.
Reeve, J. R., M. P. Ayres and P. L. Lorio, Jr. 1995. Host suitability, predation, and bark beetle population dynamics. Pages 339-357 in Cappuccino, N. and P. W. Price, editors. Population dynamics: New approaches and synthesis. Academic Press, San Diego, CA.
Sartwell, C., R. F. Scmitz, and W. J. Buckhorn. 1971. Pine engraver, Ips pini in the western states. Forest Pest Leaflet 122. USDA Forest Service, Washington, D.C.
Schenk, J. A. and D. M. Benjamin. 1969. Notes on the biology of Ips pini in central Wisconsin jack pine forests. Annals of the Entomological Society of America 62:480-485.
Swanholm, M. 1978. Lumbering in the Last of the White-Pine States. Minnesota Historic Sites Pamphlet Series No. 17. Minnesota Historical Society, St. Paul, MN.
Turchin, P., A. D. Taylor, and J. D. Reeve. 1999. Dynamical role of predators in population cycles of a forest insect: an experimental test. Science 285:1068-1071.
U.S. Global Change Research Program. 2000. Climate change impacts on the United States: the potential consequences of climate variability and change. http://www.gcrio.org/NationalAssessment/
USGS. 2003a. USGS 05275000 Elk River near Big Lake, MN. http://waterdata.usgs.gov/mn/nwis/uv?05275000
USGS. 2003b. USGS 05286000 Rum River near St. Francis, MN. http://waterdata.usgs.gov/mn/nwis/uv?05286000
USGS. 2003c. USGS 05369000 Red Cedar River at Menomonie, WI. http://waterdata.usgs.gov/wi/nwis/uv?05369000
USGS. 2003d. USGS 05368000 Hay River at Wheeler, WI. http://waterdata.usgs.gov/wi/nwis/uv?05368000
Walker, L. C. 1998. The North American forests: geography, ecology, and silviculture. CRC Press, Boca Raton, FL.
Wisconsin Department of Natural Resources. 1996. http://www.dnr.state.wi.us/org/land/forestry/Look/highlights1996.htm#All