CHARACTERIZATION OF UPLAND/WETLAND COMMUNITY TYPES:
CHANGES TO FLATIRON LAKE BOG OVER A 24-YEAR PERIOD
A Thesis
Presented in Partial Fulfillment of the Requirements for
The Degree Master of Science in the
Graduate School of The Ohio State University
By
Stephanie R. Colwell, B.S.
* * * * *
The Ohio State University Spring 2009
Master’s Examination Committee: Approved by
Dr. Dawn Ferris, Advisor ______Dr. Don Eckert Advisor Dr. P. Charles Goebel Environment and Natural Resources Graduate Program
ABSTRACT
Flatiron Lake Bog in NE Ohio is one of the few remaining kettle-hole bogs in the state and is owned by The Nature Conservancy (TNC). In order to help refine the management of this property, three main goals were set to classify and describe Flatiron
Lake Bog. The first goal was to classify the vegetation community types within the
Flatiron Lake Bog landholding to aid in long-term planning and management of this unique resource. Seven different community types were found: mixed mesophytic forest, beech-oak-red maple forest, oak-hickory forest, aspen stands, mixed swamp, tamarack- hardwood bog, and buttonbush shrub swamp. A diversity of management issues exists in these different community types, including control of invasive species, effects of water level changes using a managed outlet structure, and agricultural runoff from neighboring landowners. The second goal of this study was to determine any changes in vegetation, water chemistry, and adjacent land use over a 24-year period. A study conducted by
Kent State in 1984 provided a baseline data set of vegetation and water chemistry for the bog, which was compared to the vegetation and water chemistry currently present to determine any changes with the changing land uses. The final goal of this study was to analyze relationships along the upland-wetland gradient with differing adjacent land uses
(forest or agriculture). All of these results will provide a knowledge base to allow TNC to better manage the Flatiron Lake Bog property.
ii
ACKNOWLEDGMENTS
There are many people who have made this project possible. I need to first thank
my advisor Dawn Ferris, and my other committee members: Charles Goebel, and Donald
Eckert for their support, revisions, and suggestions. I also want to thank the people at
The Nature Conservancy (TNC), not only for allowing me to complete this project on the
Flatiron Lake Bog landholding, but also for help with certain aspects of the work itself.
Extra thanks goes to Karen Adair, land manager for Flatiron Lake Bog for assistance in
the field with surveying in property boundaries, finding the bog within the wetland
complex (so it may have taken a couple of tries - we found it eventually), and in the
generous sharing of her knowledge on the property. I would also like to express thanks to August Froehlich, the GIS specialist for TNC in Ohio for assistance and data for creating the maps included in this thesis.
Also, thanks goes to The Ohio State University Graduate School, the School of
Environment and Natural Resources (SENR), OARDC, and the OSU Mansfield Campus for support both monetary and through the use of labs and office space. The University
Fellowship awarded to me for the 2007-2008 school year provided me with the time and money needed to get a good start on the project, funding for the second year was provided by SENR through teaching assistantships, and the seed grant provided by the
iii OSU Mansfield Campus provided the monetary support needed to complete all of the field work including purchasing of equipment.
Finally, I need to thank the people who helped with the collection of field data.
My two field assistants – Jessica Colwell for the summer of 2007 and Sandi Aupperle for the summer of 2008 – I could not have done this without you. Also to Jim Downs and
Steven Rist, who helped collect tree cores and GPS points, and especially to Jim for further help collecting water samples and elevation points. Thank you, Jim, for your love and support all through this process!
iv
VITA
March 9, 1984……………………………Born – Akron, OH
2003-2005………………………………..College Intern Ohio Environmental Protection Agency Division of Surface Water Groveport, OH
2006-2007………………………………..College Intern, Customer Service Assistant Ohio Division of Forestry Columbus, OH
2007-2008………………………………..University Fellow The Ohio State University Columbus, OH
2008-2009..………………………………Graduate Teaching Assistant The Ohio State University Columbus, OH
FIELDS OF STUDY
Major Field: Environment and Natural Resources
Minor Field: Soil Science
v
TABLE OF CONTENTS
Abstract…………………………………………………………………………… ii Acknowlegments……………………………………………………………………iii Vita…………………………………………………………………………………..v List of Tables………………………………………………………………………..viii List of Figures……………………………………………………………………. xii
Introduction…………………………………………………………………………..1
Chapters
1. Review of the Literature………………………………………………………5
1.1 Background………………………………………………………………5 1.2 History and Development of Bogs……………………………………….6 1.3 Natural Vegetation……………………………………………………….7 1.4 Hydrology and Water Chemistry…………………………………………9 1.5 Disturbances……………………………………………………………..11 1.6 Summary…………………………………………………………………17
2. Characterization of Flatiron Lake Bog: Vegetation Community Types and Soils...... 19
2.1 Introduction……………………………………………………………..19 2.2 Methods…………………………………………………………………23 2.3 Results…………………………………………………………………...32 2.4 Discussion………………………………………………………………..67 2.5 Management Implications……………………………………………….72 2.6 Conclusions………………………………………………………………74
3. Changes in Vegetation and Water Chemistry to Flatiron Lake Bog with Changing Land Uses over a 24-Year Period………………………...………..77
3.1 Introduction………………………………………………………………77
vi 3.2 Methods…………………………………………………………………..80 3.3 Results…………………………………………………………………….94 3.4 Discussion………………………………………………………………..107 3.5 Management Implications………………………………………………..118 3.6 Conclusions………………………………………………………………120
4. Interactions and Relationships across Upland/Wetland Gradients in Flatiron Lake Bog………………………………………………………………………122
4.1 Introduction………………………………………………………………122 4.2 Methods…………………………………………………………………..124 4.3 Results…………………………………………………………………….144 4.4 Discussion………………………………………………………………....177 4.5 Conclusions ……………..………………………………………………...186
List of References………………………………………………………………………190
Appendices……………………………………………………………………………..195
Appendix A: Scientific and Common Names of Plants in Flatiron Lake Bog...195
Appendix B: Representative Sample Forms for Wetland Delineation at Flatiron Lake Bog………………………………………………………………199
vii
LIST OF TABLES
1.1 Water chemistry characteristics for the different types of bog peatlands……….10
2.1 Summary of vegetation communities and their acreages and predominant soil Types within Flatiron Lake Bog..………………………………………………..32
2.2 Number of stems and basal areas per ha for all tree species in the mixed mesophytic upland forest community……………………………………………34
2.3 Relative density, relative dominance, and importance values for all tree species in the mixed mesophytic upland forest community……………………………...35
2.4 Number of stems and basal areas per ha for all shrub and sapling species in the mixed mesophytic upland forest community…………………………………….36
2.5 Relative density, relative dominance, and importance values for all shrub and sapling species in the mixed mesophytic upland forest community……………..37
2.6 Number of stems and basal areas per ha for all tree species in the oak-hickory upland forest community………………………………………………………...38
2.7 Relative density, relative dominance, and importance values for all tree species in the oak-hickory upland forest community…………………………………….39
2.8 Number of stems and basal areas per ha for all shrub and sapling species in the oak-hickory upland forest community…………………………………………...40
2.9 Relative density, relative dominance, and importance values for all shrub and sapling species in the oak-hickory upland forest community……………………40
2.10 Number of stems and basal areas per ha for all tree species in the beech-oak-red maple upland forest community………………………………………………….41
2.11 Relative density, relative dominance, and importance values for all tree species in the beech-oak-red maple upland forest community…………………………...42
viii
2.12 Number of stems and basal areas per ha for all shrub and sapling species in the beech-oak-red maple upland forest community………………………………….43
2.13 Relative density, relative dominance, and importance values for all shrub and sapling species in the beech-oak-red maple upland forest community…………..44
2.14 Number of stems and basal areas per ha for all tree species in the aspen upland forest community………………………………………………………………...45
2.15 Relative density, relative dominance, and importance values for all tree species in the aspen upland forest community…………………………………………...45
2.16 Number of stems and basal areas per ha for all shrub and sapling species in the aspen upland forest community………………………………………………….46
2.17 Relative density, relative dominance, and importance values for all shrub and sapling species in the aspen upland forest community…………………………..47
2.18 Number of stems and basal areas per ha for all tree species in the mixed shrub swamp wetland vegetation community………………………………………….48
2.19 Relative density, relative dominance, and importance values for all tree species in the mixed shrub swamp wetland vegetation community……………………..48
2.20 Number of stems and basal areas per ha for all shrub and sapling species in the mixed shrub swamp wetland vegetation community…………………………….49
2.21 Relative density, relative dominance, and importance values for all shrub and sapling species in the mixed shrub swamp wetland vegetation community……..49
2.22 Number of stems and basal areas per ha for all tree species in the buttonbush shrub swamp wetland vegetation community……………………………………50
2.23 Relative density, relative dominance, and importance values for all tree species in the buttonbush shrub swamp wetland vegetation community………………...50
2.24 Number of stems and basal areas per ha for all shrub and sapling species in the buttonbush shrub swamp wetland vegetation community……………………….51
2.25 Relative density, relative dominance, and importance values for all shrub and sapling species in the buttonbush shrub swamp wetland vegetation community..51
2.26 Number of stems and basal areas per ha for all tree species in the tamarack- hardwood bog wetland vegetation community…………………………………..52
ix
2.27 Relative density, relative dominance, and importance values for all tree species in the tamarack-hardwood bog wetland vegetation community…………………52
2.28 Number of stems and basal areas per ha for all shrub and sapling species in the tamarack-hardwood bog wetland vegetation community………………………..53
2.29 Relative density, relative dominance, and importance values for all shrub and sapling species in the tamarack- hardwood bog wetland vegetation community..53
2.30 Characteristics for the different stages of decomposition using the von Post Degrees of Humification scale…………………………………………………..55
2.31 ID codes for each distinct layer in the peat profiles from Flatiron Lake Bog…..57
2.32 Species and diameters (dbh) of cored trees from the Flatiron Lake Bog wetland complex…………………………………………………………………62
2.33 Species, ages, and estimated establishment dates for all trees cored within Flatiron Lake Bog………………………………………………………………..63
3.1 GPS coordinates, sample IDs, and collection type for water sample collection locations………………………………………………………………91
3.2 Sample IDs for water chemistry samples for the summer of 2008………………93
3.3 Vegetation species recorded in the shrub vegetation layer in either the 1984 study or the study in 2008 in Flatiron Lake Bog………………………………...99
3.4 Vegetation species recorded in the herbaceous vegetation layer in 1984 study but not in the study in 2008 in Flatiron Lake Bog……………………………...100
3.5 Vegetation species recorded in the ground vegetation layer in 1984 study but not in the study in 2008 in Flatiron Lake Bog……………………………...102
3.6 Chemical and physical characteristics of the open lake and Sphagnum mat at Flatiron Lake Bog for May-September 1984 and June-October 2008 (averaged over each summer)…………………………………………………..106
4.1 GPS coordinates, sample IDs and collection type for water sample collection locations…………………………..…………………………133
4.2 Sample IDs for water chemistry samples from upland/wetland transects and bog outflow samples……………………………………………………………136
x 4.3 Sample IDs for water chemistry samples located around the open water……..137
4.4 Soil profile description for the upland soils of UWT1…………………………159
4.5 Soil profile description for the upland soils of UWT2…………………………159
4.6 Soil profile description for the upland soils of UWT3…………………………160
4.7 Soil profile description for the upland soils of UWT4…………………………160
4.8 Soil profile description for the lagg soils of UWT1……………………………161
4.9 Soil profile description for the lagg soils of UWT2……………………………161
4.10 Soil profile description for the lagg soils of UWT3……………………………162
4.11 Soil profile description for the lagg soils of UWT4……………………………162
4.12 Soil profile description for the wetland soils of UWT1………………………..163
4.13 Soil profile description for the wetland soils of UWT2………………………..163
4.14 Soil profile description for the wetland soils of UWT3………………………..163
4.15 Soil profile description for the wetland soils of UWT4………………………..163
4.16 pH, available P, K, Ca, and Mg, and CEC for the A and B horizons of the upland/wetland transects’ upland soil profiles…………………………………164
4.17 Base saturation and total N for the A and B horizons of the upland/wetland transects’ upland soil profiles…………………………………………………..164
4.18 Elevations for the ten wells used to determine water level changes and water flow patterns at Flatiron Lake Bog………………………………………176
xi
LIST OF FIGURES
2.1 Aerial photo with property boundaries for Flatiron Lake Bog, Portage County, Ohio…………………………………………………………………...... 24
2.2 Map of the soil series on the Flatiron Lake Bog landholding……………………25
2.3 Plot design layout for sampling to determine vegetation communities in Flatiron Lake Bog………………………………………………………………..27
2.4 Map of the seven vegetation communities present within the Flatiron Lake Bog landholding………………………………………………………………….33
2.5 The von Post scale of humification for layers within the peat profiles taken from Flatiron Lake Bog………………………………………………………….57
2.6 Map of the wetland boundary determined through wetland deliniation for Flatiron Lake Bog………………………………………………………………..60
2.7 Establishment dates for tamaracks cored in the southern area of the Flatiron Lake Bog wetland complex….………………………………………….64
2.8 Establishment dates for all trees cored surrounding the open water portion of Flatiron Lake Bog………………………………………………………………..64
2.9 Establishment dates for all trees by species surrounding the open water portion of Flatiron Lake Bog…………………………………………………….65
2.10 Release dates for all trees cored at Flatiron Lake Bog…………………………..66
2.11 Release dates for all red maples cored at Flatiron Lake Bog……………………66
2.12 Release dates for all tamarack cored at Flatiron Lake Bog……………………...67
2.13 Release dates for all yellow birch cored at Flatiron Lake Bog…………………..67
xii 3.1 Aerial photo with property boundaries for Flatiron Lake Bog, Portage County, Ohio……………………………………………………………………..80
3.2 Map of the vegetation communities of Flatiron Lake Bog, Portage County, Ohio………………………………………………………………………………83
3.3 Map of the soil series on the Flatiron Lake Bog landholding……………………85
3.4 Locations of wells and grab sample in the tamarack-hardwood bog vegetation community type at Flatiron Lake Bog…………………………………………...92
3.5 Aerial photograph of Flatiron Lake Bog and the surrounding adjacent land uses from 1982…………………………………………………………………...94
3.6 Aerial photograph of Flatiron Lake Bog and the surrounding adjacent land uses from 2006…………………………………………………………………...95
3.7 Percent relative change of importance values for species in the tree vegetation layer of Flatiron Lake Bog from the summer of 1984 to the summer of 2008….97
3.8 Percent relative change of importance values for species in the shrub vegetation layer of Flatiron Lake Bog from the summer of 1984 to the summer of 2008………………………………………………………………….98
3.9 Percent relative change of importance values for species in the herbaceous vegetation layer of Flatiron Lake Bog from the summer of 1984 to the summer of 2008………………………………………………………………...101
3.10 Percent relative change of importance values for species in the ground vegetation layer of Flatiron Lake Bog from the summer of 1984 to the summer of 2008………………………………………………………………...102
3.11 Smoothed curve percentage covers for major shrub species over a transect from the open lake through 20 m from the vegetation study in 1984………….103
3.12 Smoothed curve percentage covers for major shrub species over a transect from the open lake through 20 m from the vegetation study in 2008………….104
3.13 Smoothed curve percentage covers for Sphagnum species over a transect from the open lake through 20 m from the vegetation study in 1984………….105
3.14 Smoothed curve percentage covers for Sphagnum species over a transect from the open lake through 20 m from the vegetation study in 2008………….105
xiii 3.15 Precipitation amounts for the summer of 2008 at Flatiron Lake Bog, Portage County, Ohio…………………………………………………………..107
3.16 Locations of the three known water inflow points at Flatiron Lake Bog, Portage County, Ohio.………………………………………………………….115
4.1 Aerial photo with property boundaries for Flatiron Lake Bog, Portage County, Ohio……………………………………………………………………125
4.2 Map of the vegetation communities of Flatiron Lake Bog, Portage County, Ohio……………………………………………………………………128
4.3 Map of the soil series on the Flatiron Lake Bog landholding…………………..129
4.4 Locations of the three known water inflow points and the hypothesized water flow patterns at Flatiron Lake Bog, Portage County, Ohio……………...130
4.5 Locations of wells and grab sample collection points at Flatiron Lake Bog…...134
4.6 Locations of soil profiles for the upland/wetland transects…………………….139
4.7 Locations of the vegetation transects along the upland/wetland gradient……...140
4.8 Map of the wetland boundary determined through wetland deliniation for Flatiron Lake Bog………………………………………………………………145
4.9 DCA graph for all samples within all four of the upland/wetland transects……146
4.10 DCA graph for all samples within all four of the upland/wetland transects by adjacent land use types………………………………………………………148
4.11 DCA axis 1 scores and elevations for UWT1…………………………………..149
4.12 DCA axis 1 scores and elevations for UWT2…………………………………..150
4.13 DCA axis 1 scores and elevations for UWT3…………………………………..151
4.14 DCA axis 1 scores and elevations for UWT4…………………………………..152
4.15 Jaccard’s Index scores and elevations for UWT1………………………………153
4.16 Jaccard’s Index scores and elevations for UWT2………………………………153
4.17 Jaccard’s Index scores and elevations for UWT3………………………………154
xiv 4.18 Jaccard’s Index scores and elevations for UWT4………………………………155
4.19 Wetland indicator value scores and elevations for UWT1……………………..156
4.20 Wetland indicator value scores and elevations for UWT2……………………..156
4.21 Wetland indicator value scores and elevations for UWT3……………………..157
4.22 Wetland indicator value scores and elevations for UWT4……………………..158
4.23 P concentrations for the water samples from the wetland area of the upland/wetland transects………………………………………………………..165
4.24 K concentrations for the water samples from the wetland area of the upland/wetland transects………………………………………………………..166
4.25 Ca concentrations for the water samples from the wetland area of the upland/wetland transects………………………………………………………..167
4.26 Water temperatures for the water samples from the wetland area of the upland/wetland transects……………………………………………………….168
4.27 Conductivity for the water samples from the wetland area of the upland/wetland transects……………………………………………………….169
4.28 pH values for the water samples from the wetland area of the upland/wetland transects……………………………………………………….169
4.29 Dissolved O (%) for the water samples from the wetland area of the upland/wetland transects……………………………………………………….170
4.30 P concentrations for the water samples from the lagg area of the upland/wetland transects………………………………………………………..171
4.31 K concentrations for the water samples from the lagg area of the upland/wetland transects………………………………………………………..171
4.32 Ca concentrations for the water samples from the lagg area of the upland/wetland transects………………………………………………………..172
4.33 Water temperatures for the water samples from the lagg area of the upland/wetland transects………………………………………………………..173
4.34 Conductivity for the water samples from the lagg area of the upland/wetland transects………………………………………………………………………....174
xv
4.35 pH values for the water samples from the lagg area of the upland/wetland transects…………………………………………………………………………174
4.36 Dissolved O (%) for the water samples from the lagg area of the upland/wetland transects………………………………………………………..175
4.37 Water level elevations and precipitation for the summer of 2008 for lagg area well locations in Flatiron Lake Bog……………………………………….176
4.38 Water level elevations and precipitation for the summer of 2008 for wetland area well locations in Flatiron Lake Bog……………………………..177
xvi
INTRODUCTION
Flatiron Lake Bog, located in southwest Portage County, Ohio, is one of very few
kettle-hole bog ecosystem types remaining in the state. Bogs are naturally rare in Ohio
due to current climate conditions and land uses, but are present in small numbers as relics of an earlier, colder climate. This specific area is owned by The Nature Conservancy
(TNC), and is currently closed to public access to help maintain the ecosystem.
Management in the Flatiron Lake landholding is currently confined to invasive species control due to a limited collection of information on which to base other management activities. Due to current threats to this ecosystem in the forms of global warming, changing adjacent land uses, and increasing nutrient levels, more management action needs to be implemented if the ecosystem is to be maintained in its current state.
Prior management in Flatiron Lake Bog has included the invasive species removal, as well as some water level management in one area of the wetland complex.
This area was drained due to mining to the south of the property that affected the water table, and measures were taken to bring the water level back up in an attempt to restore the area to its previous condition. A weir was placed at the outflow of the wetland complex to retain water at the desired depth. Following drainage of the area, red maple
(Acer rubrum L.) invaded and became established, which were successfully killed off
1 with the water level restoration. Sphagnum mosses and blueberry (Vaccinium
corymbosum L.) stems were also transplanted to this area in an attempt to restore the
original vegetation.
Garlic mustard (Alliaria petiolata (M. Bieb) Cavara & Grande) removal is the main management occurring currently in Flatiron Lake Bog. Volunteers are used when available to pull garlic mustard by hand or spray with herbicides. Tree-of-heaven
(Ailanthus altissima (Mill.) Swingle) was also found on the property during the completion of field work for this study, and is expected to become a high priority species for eradication. Other invasive species (multiflora rose (Rosa multiflora Thunb.), bush honeysuckle (Lonicera maackii (Rupr.) Herder), and privet (Ligustrum vulgare L.)) are not a major concern at this time, due either to very low abundances or removal is believed to be unnecessary at this time.
Flatiron Lake Bog is an area consisting of several upland vegetation communities as well as a wetland complex that includes the kettle-hole bog. The property is surrounded primarily by agriculture to the west, with the previous mining area to the
south, and some residential areas to the north and east. The only buffer surrounding the wetland complex is the upland vegetation communities located on TNC’s property, with very little continuation of natural vegetation outside of these property boundaries. The unknown effects of these surrounding land uses contribute to the difficulty present in creating an effective management plan for the area.
This research project was undertaken to assist in the characterization of Flatiron
Lake Bog, to assess potential impacts of the land uses surrounding the property, and to
2 gain a greater knowledge on the relationships kettle-hole bogs in Ohio have with their adjacent upland forests. The three main goals of this study are as follows:
1) Characterize the vegetation communities and soils within the Flatiron Lake
Bog property and delineate the wetland boundary, to assess the native
diversity, invasive species threats, and relationships between the soils and
vegetation that may have implications for the property’s management to gain
knowledge of the current environmental conditions present;
2) Assess any changes in vegetation within the kettle-hole bog over a 24-year
period with changing anthropogenic land uses surrounding the Flatiron Lake
Bog property, using a vegetation composition and water chemistry
characterization study conducted in 1984 by Andreas and Bryan (1990) and
historic aerial photos to determine relative changes in vegetation species water
chemistry, and surrounding land uses; and
3) Determine relationships among vegetation, water chemistry, and soils along
upland-wetland gradients in an Ohio kettle-hole bog wetland complex,
determine any differences in these ecotone gradients with differing adjacent
land uses, and characterize the general hydrology of Flatiron Lake Bog.
These three goals will help form a knowledge base on Flatiron Lake Bog that will assist in the creation of management plans to help maintain the current natural biodiversity and features of the site. The initial delineation of the vegetation communities will provide a basic network of different management zones, and will provide areas for prescribing more specific management activities. The increased
3 knowledge on the effects of land uses and relationships along the upland-wetland
gradient will assist in the creation of more property-wide management activities.
This study will also provide a greater understanding in knowing how these kettle- hole bogs in Ohio, one of the southernmost reaches of the ecosystem’s natural range, function and relate with their surrounding uplands. This knowledge can then be used to
apply management plans to other areas in the state with this ecosystem type. In the
future, the Flatiron Lake Bog property could be further studied to look at how buffer
zones of differing widths affect the water chemistry and vegetation of kettle-hole bogs to
assist in more landscape-level planning and management. The willingness of TNC to
allow research within this property also provides an opportunity to study more long-term
changes to kettle-hole bog ecosystems in the southern extent of their natural range with
continued surrounding anthropogenic land uses and the potential impacts of global
climate change.
4
CHAPTER 1
REVIEW OF LITERATURE
1.1 Background
Ombrotrophic bog ecosystems are those peatland wetland types with acidic water chemistry, no inputs of water from groundwater or runoff (primarily precipitation fed), and that support acidic-adapted vegetation such as Sphagnum mosses (Boelter and Verry
1977, Glaser and Siegel 1987). These ecosystems are primarily found in cool temperate or boreal regions of the world, and support a unique vegetation community that grows under very few other conditions. Over human history, however, these ecosystems have been continually altered or destroyed for various reasons. Agriculture, development, and drainage are several land use changes that have caused a severe decline in the amounts of peat bogs in the world, along with other reasons such as peat and timber harvesting and mining, and emotional reasons such as fear and trepidation (Hillman and Roberts 2006,
Hughes et al. 2008).
More recently, however, interest has shifted from a utilitarian mindset on bogs, and a new paradigm has formed resulting in a higher conservation and preservation mindset. Protection efforts globally have increased, resulting in the need for more knowledge on the natural characteristics, functions, and current changes to these
5 ecosystems. In Ireland, peatlands, including bogs, are being conserved as important habitat for rare bird species such as willow ptarmigan and Eurasian curlew (Bracken et al. 2008). A study conducted by Rochefort et al. (2003) introduces a set of guidelines for restoring bogs in North America that have been previously mined for peat, indicating the interest in this continent for the conservation of bog ecosystems. Historically, the focus for studies on bogs has been on the quality of peat for fuel and a summary of the amounts that could be extracted (Dachnowski 1912). Since the mid 20th century, more studies have been focused on the hydrology, natural vegetation, levels of degradation, microbiology, and many other ecological aspects of these ecosystem types.
1.2 History and Development of Bogs in Ohio
Bogs found in Ohio are typically kettle-hole bogs, which are naturally rare in the state because it is at the southernmost portion of their geographic range in the United
States (Andreas and Bryan 1990). These bogs create a unique ecosystem type found primarily in the northeastern portion of Ohio that were formed during the retreat of the
Wisconsinian glacier around 15,700 years before present in the Kent end moraine
(Andreas 1985, Tiner 2003). Kettle-hole bogs are formed when a large block of ice from a glacier melts, creating a depression within the landscape that is then colonized by the cool, nutrient-poor adapted species that characterize ombrotrophic bogs (Tiner 2003).
The rare nature of this ecosystem in Ohio creates the need to characterize and understand the processes and functions within the areas to help in their maintenance and preservation.
It is estimated that only four percent of the state’s peatlands (any wetland characterized by an accumulation of peat) remain and support the typical vegetation of
6 the kettle-hole bog ecosystem type (Andreas and Knoop 1992). There are only three relatively undisturbed kettle-hole bogs remaining in Ohio; all are under some sort of protection (Andreas and Bryant 1990). The first, Flatiron Lake Bog which is the focus of this study, is located in southwest Portage County, owned by The Nature Conservancy
(TNC), and closed to the general public. The second is Fern Lake Bog, in Geauga
County, which is owned by the Cleveland Museum of Natural History and has limited access to the public (Cleveland Museum of Natural History http://www.cmnh.org/site/Conservation_NaturalAreas_Map_FernLakeBog.aspx. March
31, 2009). Triangle Lake Bog, in Portage County, is the third relatively undisturbed kettle-hole bog in Ohio and is owned by the Ohio Department of Natural Resources
Division of Natural Areas and Preserves. This bog is open to the public, but has boardwalks installed to limit negative human impacts (ODNR Division of Natural Areas and Preserves http://www.dnr.state.oh.us/location/triangle/tabid/967/Default.aspx. March
31, 2009).
1.3 Natural Vegetation
Initially, after formation by melting ice blocks, kettle-hole bogs are primarily an
acidic body of water with sparse vegetation. Over time, succession begins to fill in this
area with Sphagnum mosses, and eventually with ericaceous shrubs such as blueberry
(Vaccinium spp.) until it has a concentric zonation of plant communities that surround a body of acidic open water, until the vegetation completely fills in the open water
(Schwintzer and Williams 1974). Immediately surrounding the open water is a
Sphagnum mat (which enhances its own development by creating its own acidic environment (Adema et al. 2005, Gunnarsson et al. 2000)) with other acidophilic plants
7 such as sundew (Drosera rotundifolia L.) and pitcher plants (Sarracenia purpurea L.).
Outside of this initial Sphagnum zone is a zone of shrubs such as swamp loosestrife
(Decodon verticillatus (L.) Elliot), highbush blueberry (Vaccinium corymbosum L.), huckleberry (Gaylussacia baccata (Wangenh.) K. Koch), and other herbaceous plants such as sedges (Carex spp.). Finally, the outermost ring consists of tamarack (Larix laricina (Du Roi) K. Koch) trees and other shrubs.
This zonation changes through time, though, as the bog develops and undergoes natural succession (Charman 2002). The first step in this succession is an expansion of the Sphagnum moss species. As the Sphagnum moss species accumulate, they begin to encroach on the open water area in the center. As more and more Sphagnum builds up, the floating mat is better able to support an extension of a shrub layer. The expansion of the shrub layer then in turn stabilizes the floating mat to a further extent than the mosses, and eventually, the tree zone will become able to encroach. This succession may continue until the open water area disappears, and the bog loses its open water “lake”, with a continuous mixture of the Sphagnum mosses, shrubs and tamaracks across the deepening peat layer.
The direction of this succession can also go in the opposite direction as tamaracks die in these bogs. One such case of this reverse direction of succession was recorded by
Isaak et al. (1959) in the Floating Bog Bay Creek in Itasca State Park in Minnesota.
Vegetation data and measurements as well as hummock and pool measurements were recorded over a period of time from 1946 through 1957, and aerial photos were analyzed for the area between 1939 and 1957. The tamaracks in this bog were killed by increased water levels from precipitation, which resulted in a higher amount of light hitting the
8 surface of the bog. This increased light allowed for a higher amount and diversity in the species generally found in the shrub and Sphagnum zones of a bog. Pools were also found to increase in area and depth in this bog due to the increased water levels from increased precipitation.
1.4 Hydrology and Water Chemistry
While bogs are primarily precipitation fed and not highly influenced by groundwater or surface runoff, the watershed interactions between these ecosystems and the surrounding landscape are still important (Glaser et al. 1997, Richardson 2003). Bogs may be surrounded by a poor-fen (precipitation, surface, and groundwater fed peatland) or other wetland ecosystem type which is influenced by groundwater, surface runoff, or both. Changing the land uses surrounding these peatland complexes can alter the water chemistry, structure, and functions within the fen or other wetland areas, which in turn affect the central bog ecosystem (Bubier 2007).
A study in the S-2 watershed of the U.S. Forest Service Marcell Experimental
Forest in Minnesota by Tracy (1997) found that the lagg area (ecotone between the upland and wetland ecosystem types) may be an important area for water transfer between the uplands and the wetland complex in peatland ecosystems. She also found that these areas can also be important for deep seepage into the groundwater. Due to the low hydraulic conductivity of highly decomposed peat and high bulk density of underlying mineral soil, it was determined that water within the bog flowed towards the lagg area, and that groundwater in the uplands tended to flow into this area as well.
Glaser and Siegel (1987) found similar results through the study of water levels changes and water chemistry in the Lost River Peatland in northern Minnesota. While
9 the raised bog they studied served as a groundwater recharge site for most of the year,
piezometer readings and an increase in pH from <4 at the bog surface to around 7 at a
depth of 1 m led the researchers to conclude that at least for a part of the year,
groundwater discharges into the bog.
This lagg area surrounding a kettle-hole bog can serve as the outflow of a bog.
The water moves along pathways through the upper, less decomposed peat in the bog into
the lagg, and eventually out of the wetland complex. Water leaves the bog either through
deep seepage into the groundwater or flows out of a stream outflow source into the
surrounding watershed.
The water chemistry in bogs varies along a gradient for ombrotrophic to semi-
ombrotrophic to weakly minerotrophic (Andreas and Bryan 1990) (Table 1.1).
Ombrotrophic bogs are the most acidic peatland type, with very low nutrients, low pH,
and low conductivity. Semi-ombrotrphic bogs have higher nutrients, slightly higher pH,
and higher conductivity. Weakly minerotrophic peatlands are the boundary between bogs
and fens, and are the most nutrient rich bog type, with the highest pH and conductivity.
The three remaining kettle-hole bogs in Ohio are classified as semi-ombrotrophic
(Flatiron Lake and Triangle Lake) and weakly minerotrophic (Fern Lake).
Table 1.1: Water chemistry characteristics for the different types of bog peatlands. Peatland Type Ca (mg/l) Mg (mg/l) pH Conductivity (mS/cm) Ombrotrophic 0.6-2.1 0-0.2 3.2-3.8 12-27 Semi-ombrotrophic 1.5-3.5 0.2-1.0 3.7-4.2 20-50 Weakly minerotrophic 3.5-12 1.0-1.5 4.0-6.0 25-75
In general, bogs have very low nutrients due to the water source (precipitation)
and the pH in bogs is generally at or below 4. This combination of chemical 10 characteristics results in their uniquely adapted vegetation composition, and changes in
these water chemistry characteristics results in changes to the vegetation community.
Sphagnum mosses in particular are adapted to the acidity, and perpetuate this acidity in their growth and decomposition (Charman 2002).
1.5 Disturbances
Bogs face many different disturbances, both natural and anthropogenic in nature.
Natural disturbances are important both in succession of these ecosystems and in the
maintenance of the ecosystems (Isaak et al. 1959). Fires, flooding, and local climate
changes may all be detrimental to bogs, but at the same time, many of these disturbances
prevent the encroachment of woody species and help to maintain the classic vegetation
zones associated with bog ecosystem types (Moore 2002). Without some sort of
disturbance in a bog, the area will, through natural succession, change into a forest as the
open-water bog is first overgrown by Sphagnum mosses, fills in with peat, and eventually
becomes stable enough to support larger woody vegetation.
An example of an anthropogenic disturbance that may alter the hydrology of bogs
is mining. If a water table is punctured during a mining operation, the groundwater level
may drop, resulting in a higher rate of water loss to the groundwater from a bog-wetland
complex. Mining may also occur in the bog itself and result in the loss of the ecosystem
as a whole (Andreas and Knoop 1992). Following mining, restoration of the original bog
habitat is extremely difficult or impossible.
Harvesting in bogs is often done to extract several resources. Timber, peat and
Sphagnum moss species are all harvested from bog ecosystems (Moore 2002). Many different methods are employed in the harvesting of these ecosystems for all of the
11 resources removed, and the harvesting itself impacts these environments in many ways.
The removal of the resource itself may cause ecological negative impacts, such as the
removal of peat and Sphagnum, or the negative impacts may come from the equipment used in the removals such as with peat and some timber harvesting. Also with peat and timber harvesting, the peatland is often drained, altering the hydrology of the ecosystem.
Peat is often the most harvested resource from bogs throughout the world. It has historically been used as a fuel source, and in many countries, remains an important resource for energy and heat. The harvesting of peat may also be the most detrimental form of harvesting in these ecosystem types. Peat buildup in bogs occurs over tens of thousands of years (van Seters and Price 2002), and its removal results in changes in hydrology, vegetation and water chemistry (Price and Whitehead 2004).
The harvesting of peat removes the upper layer of vegetation as well as the peat
itself. This removal may cause the loss of some bog-dependent species in the ecosystem
itself, or if conducted over large areas, in an entire country such as in Croatia (Topic and
Stancic 2005). In Croatia, most of the species that have previously been found in bog ecosystems in the country are now either extinct or rare due to losses in the number and extent of undegraded bogs.
When peat is harvested, the upper layer is generally removed, leaving the more decomposed and more compact peat that has less ability to transport water, support revegetation, and loses its ability to self-regulate the surrounding environment (Smolders et al. 2003, van Seters and Price 2002). The removal of the acrotelm, or the uppermost layer of peat that is produced by the vegetative cover that begins to break down, removes the portion of the peat that enables it to retain moisture, and allows for evapotranspiration
12 rates to exceed the rates of acquiring water through the capillary action of the remaining
peat (Price and Whitehead 2004). Losing this layer also removes the substrate on which
Sphagnum mosses regenerate, reducing or eliminating the area for recolonization
(Grosvernier et al. 1997).
When these areas harvested for peat are then re-wetted during restoration
attempts, further issues arise in the regeneration of the bog vegetation. Due to the loss of
the acrotelm layer, the surface of the bog will dry out faster than it would have originally
and become hydrophobic in the areas where the water level is low. When the area is then
re-wetted, it ponds in areas, creating areas with higher water levels than normal. Most
Sphagnum mosses cannot grow with water levels that are too high or too low, so the portions of cut-over bogs that can support this regeneration are limited (Grosvernier et al.
1997, van Seters and Price 2002, Smolders et al. 2003). Near-saturated conditions have
been shown to be the most optimal for this regeneration, but are often difficult to obtain
(Price and Whitehead 2004).
Another resource extracted from bog ecosystems is the Sphagnum moss itself
(Mitsch and Gosselink 2007). The moss is usually removed by hand, and is then sold as a horticultural medium for potting to improve the water-holding capacity of the potting soil. While this form of harvesting is less intensive than the harvesting for peat, it removes the living layer of vegetation, removing the source of diaspores for regeneration.
This also reduces the self-regulating nature of the peat layer by reducing the account of living Sphagnum that helps maintain the acidic bog environment.
The third major resource harvested from bogs is timber. Drainage of the portions of the bogs to be harvested is often the first step in timber harvesting (Locky et al. 2005).
13 Following this drainage and the subsequent removal of the tree cover, the area is more
prone to desiccation. Despite the reduction in transpiration from the trees, the
evapotranspiration rates from the surface of the bog following the removal of the shade
cover increase and result in an overall reduction in the water-holding capacity of the peat
and Sphagnum.
Historically, fires have also been a major issue in bogs following the removal of
the timber (Andreas and Knoop 1992). At least one bog in Ohio changed ecosystem types after being harvested and then experiencing fires. This bog is now a swamp forest and open marsh and has vegetation that is not representative of the original bog. The removal of timber contributes to fires in aiding in the drying out of the ecosystem and in leaving behind fuel in the form of slash.
All of these reasons for harvesting bog ecosystems result in lowered biodiversity
(Topic and Stancic 2005, Achard et al. 2006), more fragmentation of the higher quality bogs (Butovsky et al. 2004), altered hydrological regimes (van Seters and Price 2002), and difficulties in reestablishing these ecosystem types following these disturbances
(Smolders et al. 2003). Harvesting of timber, Sphagnum, and peat all make bog
ecosystems more prone to other, natural disturbances as well. Desiccation and fire are
two disturbances that become more detrimental following harvesting.
This combination of natural and anthropogenic disturbances, including the
anthropogenic disturbance of removing the natural disturbance, creates many difficulties
in the management of bog ecosystems. Different vegetation zones may require different
management activities (Cooper et al. 1997), and tradeoffs may need to occur between
desired areas of these zones. The boundary of the wetland may need to be delineated
14 first, followed by a more specific breakdown of communities to facilitate more effective
and precise management (Wells 1996). The lack of knowledge on the current conditions
and their deviations from the desired conditions may result in poor management planning
and loss of valuable aspects in the ecosystem.
Even without active anthropogenic disturbances in these bog ecosystems, humans
have many other passive disturbances. While a bog may be considered a preserve or conservation area, surrounding land uses may in part alter the ecosystem (Hughes et al.
2008). Changes in the surrounding land use may in the future prove to be more
detrimental to bog ecosystems than any of the above forms of anthropogenic disturbance
(Butovsky et al.2004, Andreas and Knoop 1992). Changes from forestland to
agricultural land to developed land all impact the hydrology and vegetation of bogs in
different ways. Agricultural land adjacent to a bog ecosystem can impact not only the
amount of water entering a bog wetland complex, but can also change the chemistry of
this runoff and can increase nutrient additions to a bog through increased atmospheric
deposition of dust. Bubier et al. (2007) found that increased nutrients (such as would be
found with adjacent agricultural land uses) can change the vegetation composition within
an ombrotrophic bog.
While placing the bog in a preserve may help to protect the bog itself and
immediately surrounding land, this changing surrounding landscape matrix may cause the
decline of the ecosystem despite efforts for preservation. This landscape matrix, as it
changes, may also result in fragmentation and isolation of bogs, limiting their use as
effective habitats for wildlife (Butovsky et al. 2004). While a bog itself may be protected
through land acquisition or conservation easements, it is not a closed ecosystem, and
15 conversion of surrounding land area from forests to anthropogenic uses can have significant effects.
Another threat that faces bogs and that may in part be furthered by disturbances in
bog ecosystems is global warming (Choi et al. 2007, Moore 2002). Harvesting of peat,
Sphagnum, and timber can all result in higher decomposition rates in bogs (natural sinks for carbon (Fraser et al. 2001)), which can result in higher levels of carbon dioxide and nitrous oxides emissions. Peat, which is harvested as a fuel source in many countries, is generally considered a carbon sink, since the deposition rates exceed the decay rates, creating a storage unit for organic carbon. Following harvests, though, this material is generally burned, and the carbon stored in it is released back into the atmosphere.
While the affects of global warming on bogs is not known for certain, some of the potential effects include displacement of vegetation species and increased rates of evapotranspiration (van der Lindon et al. 2008). Many of the species found in kettle-hole bogs in Ohio are already at the southern reaches of their natural extent. Tamarack and yellow birch, for example, are more commonly found in more northern regions than
Ohio, and with increases in the average temperature in the state, may be replaced by species better adapted to the climactic conditions of the region.
The best management option for maintaining functional bog ecosystems may be to place them in preserves. While this is not always feasible, especially in countries where peat is a major fuel source, this option is one that several countries such as Croatia
(Topic and Stancic 2006) are employing to save the remaining representatives of this ecosystem type and to hopefully protect the bog-dependent plants that mostly fall on the endangered or threatened species lists for that country.
16 In cases where preservation is not a feasible option, steps should be taken to
restore the vegetative and hydrological structure and functions of damaged bog
ecosystems to aid in the natural processes of returning the areas to more natural areas.
Results from Sphagnum regeneration studies (Grosvernier et al. 1997, Price and
Whitehead 2004) should be utilized where possible, such as retaining the upper vegetation layer to redistribute following peat harvesting, or maintaining water levels at
or near saturation for long enough periods for Sphagnum to germinate and become re-
established. Timber harvesting may be more economically directed at areas where no
drainage would be needed, or the use of low-impact harvest machinery is a possible
management option.
1.6 Summary
Bog ecosystems, and their relationships with surrounding uplands, are often complex
in their processes and functions. Although they are generally considered “closed”
ecosystems hydrologically, interactions between the water within the bog itself, any
surrounding wetlands, and the surrounding uplands may not be as simple as initially
thought, as evidenced by Tracy (1997). Management of these areas, therefore, may also
be complicated, and requires more knowledge than is usually available for a specific area
to be effectively managed to meet the landowner goals and desired outcomes. In some
cases, combined effects of land use changes, global warming, and historical disturbances
may warrant a change in the ecosystem type itself. If restoration is unattainable, it may
be better to direct the ecosystem towards a more feasible community type than generally
found in kettle-hole bogs.
17 Flatiron Lake Bog, one of three remaining relatively undisturbed kettle-hole bogs in Ohio, is currently managed by TNC, but little is actually known about the property.
The current management plan for TNC within the Flatiron Lake Bog is primarily focused on invasive species removal. The primary goal for Flatiron Lake Bog is to maintain the natural species diversity that exists within this ecosystem, as it is one of only three remaining kettle-hole bogs in Ohio. The current vegetation, hydrology, and peat and soil characteristics are needed, along with how these have changed over the past 24 years.
This data, along with an idea of the interactions that are occurring between the uplands and the bog/wetland complex, can help facilitate more effective management on this property, but can also provide insight on the processes and changes that occur in kettle- hole bogs in the southern reaches of their range.
18
CHAPTER 2
CHARACTERIZATION OF FLATIRON LAKE BOG: VEGETATION COMMUNITIES AND SOILS
2.1 Introduction
Throughout the world bogs are found primarily in the boreal and cool temperate regions of the world (Moore 2002). Bogs are wetland types that accumulate organic material (peat), have acidic water and substrate, and are exclusively or primarily precipitation fed (Moore 2002, Butovsky et al. 2004, Nordbakken et al. 2003). Due to the nature of the water source and its isolation from groundwater, bogs are nutrient-poor wetland types, and support a unique flora composition. Sphagnum mosses are often the most defining plant species in these ecosystems and their characteristics help perpetuate the acidic, nutrient-poor water chemistry (Rochefort and Vitt 1990). Due to these conditions, bogs often support populations of rare plant species, whether at a local, regional or global scale (Topic and Stancic 2006, Butovsky et al. 2004).
Historically, the anthropogenic view of bogs has been utilitarian in nature (Mitsch and Gosselink 2007). On the global scale, bogs have been areas of high conversion to agricultural uses due to the high amounts of organic material, which after drainage results in productive farm land. Peat has been and still is used as a source of fuel in many areas, and Sphagnum mosses are harvested for horticultural purposes. Throughout the past
19 century, however, focus in bog ecosystems has slowly shifted to a more conservation-
based mindset (Butovsky et al. 2004, Topic and Stancic 2006, Tiemeyer et al. 2006).
Throughout the nineteenth and early twentieth centuries, Ohio peatlands were seen primarily as a resource for peat and sphagnum and as productive agricultural land once drained (Dachnowski 1912). Alfred Dachnowski’s Geological Survey of Ohio publication entitled Peat Deposits of Ohio: Their origin, formation, and uses (1912) is a survey of the location and quality of peatlands across the state. He lists after the name of each peatland surveyed a description of its location, size, quality of peat as a fuel, and potential productivity of the land if used for agriculture. This publication clearly outlines the prevailing view of the importance of peatland utilization during this time period.
More recently the focus has changed from how to best utilize and exploit peatlands to more of an emphasis on how to conserve and protect these ecosystem types
(Tomassen et al. 2004). One example of this changing paradigm with respect to bog ecosystems is in Ohio. It is estimated that only four percent of the state’s peatlands remain and support the typical vegetation of the ecosystem type (Andreas and Knoop
1992), and there are currently only three relatively undisturbed kettle-hole bogs left in
Ohio, all of these under some sort of protection (Andreas and Bryant 1990). Flatiron
Lake Bog, located in southwest Portage County, is owned and protected by The Nature
Conservancy (TNC) and is closed to all public admittance. Fern Lake Bog, in Geauga
County, is a Cleveland Museum of Natural History Natural Area with limited access to
the public (Cleveland Museum of Natural History
http://www.cmnh.org/site/Conservation_NaturalAreas_Map_FernLakeBog.aspx. March
31, 2009). Triangle Lake Bog, in Portage County, is the third relatively undisturbed
20 kettle-hole bog in Ohio and is owned by the Ohio Department of Natural Resources
Division of Natural Areas and Preserves. This bog is open to the public, but has boardwalks installed to limit human impacts (ODNR Division of Natural Areas and
Preserves http://www.dnr.state.oh.us/location/triangle/tabid/967/Default.aspx. March 31,
2009).
Flatiron Lake Bog, which is the focus of this study, has had a diverse and interesting history (personal communication, Adair June 6, 2007). The bog has been used by locals in the area for at least several generations as a place to collect blueberries. One neighboring landowner (personal communication, Brooker June 6, 2007) recalls a road that entered into the Flatiron Lake Bog landholding that allowed people to enter the bog to harvest blueberries, which was allowed by the owner at the time if one quart of blueberries were given as payment for every three or four quarts collected. These were then sold at a roadside stand to those who did not want to pick their own.
In the early-mid 1900’s, the area was planned to be mined for gravel and sand.
For a variety of reasons, and several versions currently are passed through the local lore, the mining operation was halted, saving the bog. Remnants of this planned operation are still evident in scattered abandoned equipment, washing pits, and a retainment wall of logs.
Current threats to the bog are different than those that were faced in the past.
Invasive species are a major concern in the management of Flatiron Lake Bog. Garlic mustard (Alliaria petiolata (M. Bieb) Cavara & Grande), multiflora rose (Rosa multiflora
Thunb.), glossy buckthorn (Rhamnus frangula Mill.), autumn-olive (Elaeagnus umbellate
Thunb.), and tree-of-heaven (Ailanthus altissima (Mill.) Swingle) are all present in the
21 upland areas of the landholding, and in many areas, these invasives dominate the upland
understory of the forest communities. Accelerated rates of woody encroachment within
the bog is another threat. While this is a natural occurrence in the succession of bogs, red
maple (Acer rubrum L.) is currently encroaching in the wetland complex, which may be
problematic in this type of ecosystem. The transpiration rates associated with red maple
may reduce the water levels in the wetlands, drying out the substrate and allowing for
more red maples to colonize, creating a negative feedback loop (Charman 2002). The
root systems of red maple in wetland ecosystems is shallow and spread out, allowing for
the uptake, and therefore the transpiration, of high amounts of water from the surface are
of the wetland (Hutnick and Yawney 1961).
Another management issue that Flatiron Lake Bog is facing is poaching of the
rare bog plants. Pitcher plants (Sarracenia purpurea L.), sundews (Drosera rotundifolia
L.), and orchids are all present in the Sphagnum mat zone of the bog and are valued as ornamental plants. The damaged caused by this issue is twofold. The removal of the plants themselves is the major issue, but there is also damage caused by the poachers walking across the mat. Other forms of destruction are also occurring from trespassing by hikers, ATV riders, horseback riders, and people harvesting blueberries. While the bog is held as a preserve closed to the public, problems still exist due to trespassing.
The goal of this study is to characterize the Flatiron Lake Bog landholding. The
objectives set to meet this goal include: classification of vegetation communities across
the entire TNC landholding; peat and soil profile characterizations; tree core analyses for establishment dates and releases; and a wetland delineation. These community types,
peat characterizations, tree establishment and release dates, as well as the delineation of
22 the wetland boundary can then be utilized by TNC for future planning and management
of the entire landholding. The vegetation communities can be used as management units,
in which specific management actions can be undertaken on a more localized scale where they are needed the most. The peat and soil characterizations will provide greater insight into the spatial distribution of specific vegetation species and communities.
2.2 Methods
Study Area Description
Flatiron Lake Bog is located in the southwestern corner of Portage County, Ohio
(N 41˚ 2’; W 81˚ 22’) and is one of the three remaining relatively undisturbed kettle-hole
bogs remaining in Ohio. TNC currently owns this bog, its surrounding wetland complex,
and an area of uplands surrounding this complex (Figure 2.1). The entire landholding is
39.2 hectares. The area is not open to the public due to the sensitive nature of the
Sphagnum mat and the potential damage that can be caused by human disturbances.
The bog is located within the Little Cuyahoga River watershed (Subwatershed number 04110002-030-050), which ultimately drains north into Lake Erie
(http://www.oh.nrcs.usda.gov/technical/14-digit/14narr04110002.html, accessed April 2,
2009). This watershed drains 4773.7 ha, from below the Mogadore Reservoir (Portage
County, Ohio) to the Springfield Lake outlet (Summit County, Ohio). The Flatiron Lake
Bog landholding constitutes 0.7 percent of the Little Cuyahoga Watershed.
23
Figure 2.1: Aerial photo and boundary of the Flatiron Lake landholding, Portage County, Ohio (map created by TNC August 18, 2004).
This bog is representative of the concentric zones of vegetation typical of this
type of kettle-hole bogs in the open water lake successional stage. The open water area is
surrounded by a floating Sphagnum mat with swamp loosestrife and sundew and pitcher-
plants interspersed on the higher hummocks of the area. Surrounding the mat is a layer
of shrubs (primarily swamp loosestrife (Decodon verticillatus (L.) Elliot), highbush
blueberry (Vaccinium corymbosum L.), and huckleberry (Gaylussacia baccata
(Wangenh.) K. Koch)) with a ground layer of Sphagnum, sundew, sedges (Carex spp.), pitcher plants, and other herbaceous species. Outside of the shrub zone is a ring of tamaracks (Larix laricina (Du Roi) K. Koch), yellow birch (Betula alleghaniensis 24 Britton), and red maple. The tamarack trees are at the southernmost extreme of their natural distribution (http://plants.usda.gov/java/profile, accessed April 3, 2009).
The soil in the bog and surrounding wetland complex is Carlisle muck (euic, mesic, typic Medisaprists), which is a very poorly drained Histosol (USDA Soil
Conservation Service 1978). This soil series has moderately rapid permeability and high available water capacity. The soil series on the upland portions of the Flatiron Lake Bog landholding include Chili (fine-loamy, mixed, mesic, typic Hapludalf) silt loam, 2 to 6 percent slopes, Chili gravelly loam, 6 to 12 percent slopes that are moderately eroded,
Sebring silt loam (fine-silty, mixed, mesic, typic Ochraqualfs), Chili-Wooster (Wooster – fine-loamy, mixed, mesic, typic Fragiudalfs) complex, 6 to 12 percent, 12 to 18 percent, and 18 to 30 percent slopes, Chili-Oshtemo (Oshtemo – coarse-loamy, mixed, mesic, typic Hapludalfs) complex, 12 to 18 and 18 to 25 percent slopes, and gravel pits (Figure
2.2). The parent material of the area is glacial till deposits of the Kent Moraine, which consists of high amounts of gravel and was deposited by a succession of glaciers and glacial retreats, from approximately 40,000 years before present until 15,700 years before present (Andreas and Bryan 1990).
25
Figure 2.2: Soils of the Flatiron Lake Bog landholding, Portage County, Ohio. Vegetation Community Delineation
Transects running north-south were distributed across the Flatiron Lake Bog landholding during the summer of 2007. Vegetation samples were taken along these transects, with 67 m between the transect lines and 60.4 m between plots along these transect lines. Each vegetation plot consisted of three nested plots for different
vegetation measurements (Figure 2.3). A 400 m² circular plot was used for all trees,
taken as all woody vegetation greater than or equal to 10 cm dbh (diameter at breast
height, or 1.37 m). For each tree within this plot, species (from the USDA Plants
Database, Appendix A), diameter, and whether it was living or dead were recorded.
Nested within the 400 m² plot was a 25 m² circular plot for all saplings and shrubs.
Saplings and shrubs were determined as woody vegetation less than 10 cm diameter and greater than 1.37 m tall. Each stem was recorded by species and placed into diameter classes of less than 2.5 cm, 2.5 to 4.9 cm, 5.0 to 7.4 cm, and 7.5 to 9.9 cm. Finally, a
26 quadrat (0.5 m², subdivided into eight 25 x 25 cm subquadrats) was used to record all
herbaceous plants and woody regeneration under 1.37 m tall. A Daubenmire frame was
used to record each species in the plot, along with its percent cover and abundance.
Frequency was measured as the number of 25 x 25 cm subquadrats in which each species
was present.
Figure 2.3: Vegetation plot design layout. Outer circular plot is 400 m² for all trees, inner circular plot is 25 m² for all saplings and shrubs, and inner rectangle is ½ m² for all herbaceous vegetation.
To summarize the overstory vegetation, the basal area for each of the live trees
was calculated, and total basal area for each species was calculated for every plot. Based
on these calculations, relative dominance and relative densities were calculated for each
species on all of the plots using the formulas:
Relative dominance = (total species basal area)/(total plot basal area)
Relative density = (total stems of species)/(total stems of plot)
Importance values were then found for each species by plot by taking the average of the
relative density and relative dominance for that species.
27 Basal areas for each species on all of the plots were also calculated for the sapling
and shrub vegetation. This was completed using the midpoint of the diameter class as the
diameter (e.g., 3.8 cm diameter for the 2.6-5.0 cm diameter class). Relative dominance,
relative density, and importance values were then calculated by using the same formulas
as above for each sapling and shrub species by plot.
For each species recorded in the quadrats, abundance was recorded as the number
of subquadrats the species was found in. The Daubenmire frame was divided into 25 x
25 cm subquadrats, and the abundance of each species was recorded as the total number
of these that it was present in. Relative frequency for each of these species was
calculated per plot by the following formula:
Relative frequency = (# subplots species found in)/8
Relative dominance for each species was calculated based on the percent cover
measurements in each plot using the formula:
Relative dominance = (% cover of species)/[Σ(% cover of all species)]
Importance values were than taken as the average of each species’ relative frequency and relative dominance.
Following determination of the different vegetation community types, stand characteristics were calculated for each community type individually. For each tree species within the community type, basal area and density per hectare were calculated along with relative dominance, relative density, and importance values. Plots were grouped into these community types and for each shrub and herbaceous species, relative density, relative dominance and importance values were also calculated on a per hectare
28 basis. The vegetation communities as delineated by Anderson (1982) were then reclassified into the vegetation communities used by TNC.
Peat Profiles
The peat resource of Flatiron Lake Bog was characterized along a transect
running from the south end of the open water portion of the bog south through the
wetland complex to the interior edge of the lagg. Five samples were characterized to a
minimum depth of 70 cm, and samples were taken from each horizon in these profiles.
Sample depths were determined by the maximum depth that could be sampled with the
soil auger used due to roots, water levels, and length of the auger. The von Post scale of
humification (von Post 1924) was used to determine the level of decomposition in each of
these profile horizons.
Wetland Delineation
Delineation of the wetland boundary was conducted to determine the boundary of
the wetland complex surrounding the open water bog. Delineation of this area was
completed using the 1987 U.S. Army Corp of Engineers Wetland Delineation Manual
during late June and early July 2008. All common vegetation species were recorded, and
the percent of wetland obligates and facultative wetland species was determined based on
the total number of common plant species found in each sample. Standing water and
other hydrological indicators such as redoxymorphic features in the soil and water lines
on vegetation were recorded, and soil profiles were characterized including horizons,
texture, color, presence and abundance of coarse fragments, and presence, colors and
abundance of redoxymorphic features.
29 Delineation plots were established approximately every 20 m around the wetland edge. Each plot consisted of three samples: the first in an area of the wetland edge with standing water or water at the surface, the second within the boundary area with no obvious surface hydrological indicators, and the third in the edge of the upland area with no hydrological indicators and a change in elevation. Samples within the plots were determined to be within the wetland if the requirements for all three wetland indicators
(hydrology, hydric soils, and hydrophytic vegetation) were met. If one or more indicators were not met, the sample was determined to be within the upland. Sample field sheets are included in Appendix B.
Tree Core Analysis
To supplement the characterization of Flatiron Lake Bog, tree increment cores were taken on 37 trees within the wetland complex including: tamarack (29 cores), yellow birch (four cores), and red maple (four cores). These samples were taken to reflect the relative density of these three species in the tree vegetation zone surrounding the open water portion of the bog. Trees to be sampled were determined along four transects surrounding this open water portion of the bog in the four cardinal directions and in a small area of tamaracks in the southern portion of the wetland complex.
Cores were analyzed using WinDENDRO (Régent Instruments 2003) to determine tree ages and to compare establishment dates within and between species. The age determined by WinDENDRO was used as the actual age if the pith was hit during the coring process. It the core did not cross the pith, pith indicators were used to estimate the actual age and establishment year. Establishment years for both the tamaracks and red maples surrounding the open water bog were determined and annual growth rates were
30 compared to determine when the red maples became established in the bog area and how quickly they are growing compared to the tamaracks. Cores taken from the tamaracks in the southern portion of the wetland complex were then compared with those taken from the area surrounding the open water to compare establishment dates and growth rates.
Release years for all trees were determined following adapted methodology from
Bergeron and Brisson (1990). A release was determined by finding years in which the growth was doubled within three following years, and that had double the growth in the
10 years following release (average) than during the previous 10 years average.
Statistical Analysis
In order to delineate the vegetation communities, a cluster analysis was run using the importance values for the common overstory tree species and sapling/shrub species for each plot. Common tree and sapling/shrub species were those found in more than five percent of the total vegetation community plots (92). These plots were then divided into two groups: those located in the wetland area of the landholding and those located in the upland areas of the landholding. Soils data, such as soil series, percent slope, and landform (from the Portage County Soil Survey (USDA Soil Conservation Service
1978)) was also included in the analysis.
The cluster analysis was conducted using PC-ORD 5 (McCune and Mefford
1999) with Ward’s linkage method and the relative Euclidean distance measure.
Community types were then separated using a combination of the information ratings and the vegetation community guidelines presented by Anderson (1982). Plots were split into different vegetation communities when the information ratings were 50 percent or lower, and when plots were similar in vegetation composition as the communities outlined by
31 Anderson (1982). These initial community divisions were then modified to eliminate outlier plots based on their locations on aerial photos. Vegetation communities were then classified based on the TNC manual for vegetation communities (Faber-Langendoen
2001) in addition to the Anderson (1982) communities.
2.3 Results
Vegetation Community Delineation
Seven community types were delineated using the cluster analysis results, the
Anderson (1982) vegetation community guide, and locations of plots within the landholding (Table 2.1, Figure 2.4). Four of these communities are located in the upland portions of Flatiron Lake Bog: mixed mesophytic forest, oak-hickory forest, beech-oak- red maple forest and an aspen stand. The remaining three community types are located in the wetland portions of Flatiron Lake Bog: buttonbush shrub swamp, mixed shrub swamp and tamarack-hardwood bog.
Table 2.1: Areas and predominant soil series for the vegetation communities of Flatiron Lake Bog, Portage County, Ohio. Vegetation Community Area (ha) Soil Series Chili-Wooster Complex Mixed Mesophytic 12.2 Chili-Oshtemo Complex Oak-Hickory 4.2 Chili Chili Beech-Oak-Red Maple 9.2 Chili-Wooster Complex Aspen 1.2 Gravel Pits Mixed Shrub Swamp 8.9 Carlisle Muck Buttonbush Swamp 2.4 Carlisle Muck Tamarack-Hardwood Bog 1.1 Carlisle Muck Total 39.2
The mixed mesophytic forest community type is the largest upland vegetation community, consisting of 12.2 ha. It was characterized by an overstory dominated by red maple, black cherry (Prunus serotina Ehrh.) and sassafras (Sassafras albidum (Nutt.) 32 Nees) (Table 2.2). These three dominant species constituted nearly 75 percent of the total importance values for the tree layer. On average, this community type had 552 (±192.37) trees per ha, and an average total basal area of 35.46 (± 10.43) m² per ha (Table 2.3).
There was a total of 20 tree species in this community type.
33
Figure 2.4: Vegetation communities for Flatiron Lake Bog, Portage County, Ohio. Map created on October 28, 2008.
34 The shrub layer of the mixed mesophytic community type was dominated by red
maple, multiflora rose and black cherry. Invasive species were high in this layer, and
included privet and bush honeysuckle in addition to the multiflora rose. These invasive
species had an average combined importance value of 37.93 percent (Table 2.4). In the
shrub and sapling layer, this community type had an average of 6,566.67 (± 4,523.82) stems per ha and an average basal area of 2.10 (± 2.59) m² per ha (Table 2.5).
Table 2.2: Number of stems and basal area per ha for all tree species within the mixed mesophytic vegetation community type in Flatiron Lake Bog, Portage County, Ohio. Numbers in parenthesis indicate standard deviation from the mean of all sample plots in the community. Species Number of Stems/ha Basal Area (m²/ha) Acer rubrum 209.38 (162.49) 11.25 (7.39) Acer saccharum 1.04 (5.10) 0.06 (0.27) Betula alleghaniensis 7.29 (20.16) 0.32 (0.90) Carya glabra 2.08 (10.21) 0.23 (1.14) Cornus florida 2.08 (7.06) 0.02 (0.06) Crataegus spp. 3.13 (11.21) 0.05 (0.17) Fagus grandifolia 1.04 (5.10) 0.02 (0.10) Fraxinus pennsylvanica 1.04 (5.10) 0.01 (0.06) Liriodendron tulipifera 46.88 (68.09) 4.79 (8.00) Magnolia acuminata 3.13 (8.45) 0.09 (0.29) Nyssa sylvatica 4.17 (12.04) 0.05 (0.16) Populus deltoides 5.21 (18.03) 1.06 (4.54) Populus grandidentata 13.54 (44.83) 0.99 (3.07) Prunus serotina 136.46 (101.61) 9.72 (7.59) Quercus alba 3.13 (8.45) 0.59 (1.76) Quercus rubra 3.13 (15.31) 0.35 (1.74) Quercus velutina 6.25 (21.17) 1.26 (4.36) Sassafras albidum 90.63 (137.09) 4.06 (5.89) Ulmus americana 11.46 (42.97) 0.18 (0.66) Ulmus rubra 1.04 (5.10) 0.35 (1.70) Total 552.08 (192.37) 35.46 (10.43)
35 Table 2.3: Relative density, relative dominance and importance values for all tree species within the mixed mesophytic vegetation community type in Flatiron Lake Bog, Portage County, Ohio. Numbers in parenthesis indicate standard deviation from the mean of all sample plots in the community. Relative Relative Importance Species Density Dominance Value (%) Acer rubrum 36.66 (20.75) 31.66 (17.46) 34.17 (17.27) Prunus serotina 26.56 (18.26) 28.19 (22.32) 27.38 (19.34) Sassafras albidum 14.68 (20.31) 11.85 (19.03) 13.28 (19.38) Liriodendron tulipifera 9.75 (14.07) 13.74 (21.15) 11.75 (1.25) Populus grandidentata 2.20 (7.33) 2.28 (7.15) 2.24 (7.17) Populus deltoides 0.76 (2.60) 3.19 (12.05) 1.97 (7.29) Quercus velutina 1.43 (4.33) 2.27 (7.77) 1.85 (5.99) Ulmus americana 1.80 (6.82) 0.86 (3.00) 1.33 (4.88) Ulmus rubra 1.04 (5.10) 1.13 (5.41) 1.06 (5.20) Quercus alba 0.56 (1.54) 1.44 (4.29) 1.00 (2.83) Betula alleghaniensis 1.09 (3.12) 0.83 (2.37) 0.97 (2.72) Quercus rubra 0.37 (1.80) 0.94 (4.61) 0.65 (3.21) Magnolia acuminata 0.70 (1.97) 0.47 (1.73) 0.59 (1.81) Nyssa sylvatica 0.68 (1.94) 0.23 (0.80) 0.46 (1.34) Carya glabra 0.40 (1.94) 0.42 (2.07) 0.41 (2.01) Crataegus spp. 0.37 (1.24) 0.16 (0.66) 0.26 (0.92) Acer saccharum 0.17 (0.82) 0.23 (1.15) 0.20 (0.98) Cornus florida 0.27 (0.93) 0.05 (0.21) 0.16 (0.56) Fraxinus pennsylvanica 0.32 (1.57) 0.02 (0.09) 0.16 (0.83) Fagus grandifolia 0.19 (0.97) 0.04 (0.18) 0.11 (0.58) Total 100 100 100
36 Table 2.4: Number of stems and basal area per ha for all shrub and sapling species within the mixed mesophytic vegetation community type in Flatiron Lake Bog, Portage County, Ohio. Numbers in parenthesis indicate standard deviation from the mean of all sample plots in the community. * indicates an invasive species. Species Number of Stems/ha Basal Area (m²/ha) Acer rubrum 466.67 (918.73) 1.0717 (2.28) Amelanchier spp. 33.33 (163.30) 0.0041 (0.02) Betula alleghaniensis 16.67 (81.65) 0.1002 (0.49) Carya glabra 33.33 (112.93) 0.0205 (0.09) Cornus florida 66.67 (152.28) 0.0900 (0.27) Crataegus spp. 16.67 (81.65) 0.0205 (0.09) Fagus grandifolia 50.00 (244.95) 0.0061 (0.03) Fraxinus americana 16.67 (81.65) 0.0020 (0.01) Fraxinus pennsylvanica 133.33 366.73) 0.0164 (0.05) Hamamelis virginiana 150.00 (654.75) 0.0184 (0.08) Ligustrum vulgare* 150.00 (329.69) 0.0184 (0.04) Liriodendron tulipifera 66.67 (192.62) 0.0082 (0.02) Lonicera maackii* 166.67 (735.83) 0.0205 (0.09) Prunus serotina 466.67 (733.47) 0.0900 (0.15) Quercus alba 16.67 (81.65) 0.0020 (0.01) Rosa multiflora* 3133.33 (3582.89) 0.3439 (0.40) Rubus allegheniensis 166.67 (539.46) 0.0302 (0.09) Sassafras albidum 33.33 (163.30) 0.0368 (0.18) Ulmus americana 66.67 (225.86) 0.0082 (0.03) Ulmus rubra 33.33 (112.93) 0.0041 (0.01) Vaccinium corymbosum 816.67 (3343.48) 0.1002 (0.41) Viburnum prunifolium 33.33 (163.30) 0.0041 (0.02) Viburnum recognitum 400.00 (800.00) 0.0430 (0.96) Vitis riparia 33.33 (112.93) 0.0389 (0.13) Total 6,566.67 (4523.82) 2.098 (2.59)
37 Table 2.5: Relative density, relative dominance and importance values for all shrub and sapling species within the mixed mesophytic vegetation community type in Flatiron Lake Bog, Portage County, Ohio. Numbers in parenthesis indicate standard deviation from the mean of all sample plots in the community. * indicates an invasive species. Relative Relative Importance Value Species Density Dominance (%) Rosa multiflora* 40.08 (37.06) 29.56 (32.36) 34.82 (33.80) Acer rubrum 10.39 (21.22) 19.75 (35.66) 15.07 (27.91) Prunus serotina 14.62 (24.89) 14.46 (25.62) 14.55 (25.21) Vaccinium corymbosum 7.08 (21.31) 7.08 (21.31) 7.08 (21.31) Viburnum recognitum 4.34 (7.53) 3.13 (6.91) 3.75 (7.06) Cornus florida 2.55 (7.52) 4.34 (11.45) 3.45 (9.28) Rubus allegheniensis 2.13 (6.33) 3.74 (13.78) 2.93 (9.88) Fagus grandifolia 3.13 (15.31) 1.43 (6.99) 2.28 (11.15) Vitis riparia 0.43 (1.52) 3.42 (12.39) 1.92 (6.81) Ligustrum vulgare* 1.93 (4.26) 1.56 (3.34) 1.75 (3.57) Ulmus rubra 1.91 (7.16) 1.42 (6.80) 1.66 (6.88) Fraxinus pennsylvanica 1.61 (5.34) 1.52 (5.26) 1.57 (5.30) Hamamelis virginiana 2.28 (8.35) 0.62 (2.28) 1.45(5.31) Lonicera maackii* 1.92 (7.54) 0.80 (2.72) 1.36 (4.97) Carya glabra 0.38 (1.33) 1.63 (7.35) 1.00 (4.29) Crataegus spp. 0.30 (1.12) 1.41 (6.56) 0.85 (3.80) Liriodendron tulipifera 1.22 (3.86) 0.43 (1.19) 0.82 (2.49) Sassafras albidum 0.20 (1.00)) 1.32 (6.45) 0.76 (3.72) Ulmus americana 1.16 (4.33) 0.16 (0.54) 0.65 (2.41) Betula alleghaniensis 0.30 (1.46) 0.95 (4.6) 0.64 (3.01) Viburnum prunifolium 0.53 (2.61) 0.52 (2.55) 0.52 (2.55) Amelanchier spp. 0.83 (4.08) 0.07 (0.36) 0.45 (2.22) Fraxinus americana 0.42 (2.04) 0.42 (2.04) 0.42 (2.04) Quercus alba 0.26 (1.28) 0.26 (1.28) 0.26 (1.28) Total 100 100 100
In the oak-hickory forest vegetation community (4.2 ha), the dominant tree species were black oak (Quercus velutina Lam.), red maple, red oak (Quercus rubra L.),
white oak (Quercus alba L.) and bitternut hickory (Carya cordiformis (Wangenh.) K.
Koch). Other species of oak and hickory were also present in this vegetation community
in addition to other genera, for a total of 16 tree species. This vegetation community had
an average of 469 (±129.3) total stems per ha and an average total basal area of 45.08 (±
38 18.36) m² per ha (Table 2.6). Red maple has the highest importance value in this vegetation community, with an average value of 35.25 percent. This is followed by red and black oak (Table 2.7).
Table 2.6: Number of stems and basal area per ha for all tree species in the oak-hickory forest vegetation community in Flatiron Lake Bog, Portage County, Ohio. Numbers in parenthesis indicate standard deviation from the mean of all sample plots in the community. Species Number of Stems/ha Basal Area (m²/ha) Acer rubrum 191.67 (81.42) 11.1547 (7.09) Betula alleghaniensis 14.58 (24.91) 0.6307 (1.18) Carya cordiformis 27.08 (53.79) 1.0603 (2.02) Carya ovata 2.08 (7.22) 0.0358 (0.12) Cornus florida 6.25 (11.31) 0.1302 (0.28) Fagus grandifolia 4.17 (9.73) 0.4707 (1.12) Liriodendron tulipifera 2.08 (7.22) 0.0383 (0.13) Magnolia acuminata 6.25 (15.54) 0.5460 (1.50) Nyssa sylvatica 50.00 (89.19) 2.5769 (5.90) Prunus serotina 12.50 (16.85) 0.3906 (0.79) Quercus alba 50.00 (47.67) 5.4050 (5.76) Quercus bicolor 4.17 (14.43) 0.0776 (0.27) Quercus palustris 2.08 (7.22) 0.3284 (1.14) Quercus rubra 52.08 (65.24) 10.5341 (16.48) Quercus velutina 29.17 (41.06) 11.3897 (16.72) Sassafras albidum 14.58 (24.91) 0.3127 (0.54) Total 468.75 (129.30) 45.08 (18.36)
39 Table 2.7: Relative density, relative dominance and importance values for all tree species in the oak-hickory forest vegetation community in Flatiron Lake Bog, Portage County, Ohio. Numbers in parenthesis indicate standard deviation from the mean of all sample plots in the community. Relative Relative Importance Value Species Density Dominance (%) Acer rubrum 41.17 (18.82) 29.33 (20.44) 35.25 (15.19) Quercus velutina 7.42 (11.17) 21.68 (30.05) 14.55 (20.52) Quercus rubra 9.85 (9.83) 18.88 (21.12) 14.37 (15.18) Quercus alba 10.06 (10.01) 13.41 (13.60) 11.73 (11.75) Nyssa sylvatica 9.52 (13.93) 5.50 (10.18) 7.51 (11.88) Carya cordiformis 6.4 (12.64) 2.39 (5.13) 4.39 (8.62) Betula alleghaniensis 3.15 (5.93) 1.61 (3.27) 2.38 (4.59) Sassafras albidum 3.65 (6.61) 1.12 (1.91) 2.38 (4.21) Magnolia acuminata 1.37 (3.34) 1.96 (6.07) 1.66 (4.61) Prunus serotina 2.34 (3.02) 0.66 (1.33) 1.50 (2.01) Fagus grandifolia 0.97 (2.30) 1.78 (4.27) 1.39 (3.28) Cornus florida 1.64 (2.97) 0.37 (0.80) 1.00 (1.83) Quercus palustris 0.6 (2.06) 1.07 (3.72) 0.84 (2.89) Quercus bicolor 1.04 (3.61) 0.13 (0.45) 0.59 (2.03) Carya ovata 0.52 (1.80) 0.06 (0.21) 0.29 (1.01) Liriodendron tulipifera 0.30 (1.03) 0.05 (0.17) 0.17 (0.60) Total 100 100 100
The shrub and sapling layer of the oak-hickory forest vegetation community,
which had an average of 4768.8 (± 3,775.39) stems per ha and 2.65 (± 2.02) m² basal area
per ha (Table 2.8), and is dominated by highbush blueberry, red maple and witch-hazel
(Hamamelis virginiana L.) (Table 2.8). The oak-hickory vegetation community had 15
shrub and sapling species, none of which were invasive.
40 Table 2.8: Number of stems and basal area per ha for shrub and sapling species within the oak-hickory forest vegetation community in Flatiron Lake Bog, Portage County, Ohio. Other species includes: wild grape, serviceberry, hawthorn and maple-leaf viburnum. Numbers in parenthesis indicate standard deviation from the mean of all sample plots in the community. Species Number of Stems/ha Basal Area (m²/ha) Acer rubrum 833.3 (771.46) 1.3458 (1.42) Betula alleghaniensis 33.3 (115.47) 0.1023 (0.35) Cornus florida 133.3 (260.54) 0.0491 (0.12) Fagus grandifolia 33.3 (115.47) 0.0409 (0.13) Hamamelis virginiana 866.7 (1625.55) 0.4663 (1.31) Magnolia acuminata 66.7 (230.94) 0.0082 (0.03) Nyssa sylvatica 433.3 (1098.21) 0.2168 (0.51) Prunus serotina 600 (844.23) 0.1064 (0.20) Quercus rubra 33.3 (115.47) 0.0368 (0.13) Sassafras albidum 66.7 (155.70) 0.1023 (0.35) Vaccinium corymbosum 1,033.3 (3220.20) 0.1268 (0.40) Other shrub species 166.7 (360.13) 0.0041 (0.01) Total 4,768.8 (3,775.39) 2.6548 (2.02)
Table 2.9: Relative density, relative dominance and importance values for shrub and sapling species within the oak-hickory forest vegetation community in Flatiron Lake Bog, Portage County, Ohio. Other species includes: wild grape, serviceberry, hawthorn and maple-leaf viburnum. Numbers in parenthesis indicate standard deviation from the mean of all sample plots in the community. Relative Relative Importance Value Species Density Dominance (%) Acer rubrum 26.33 (25.36) 44.38 (38.82) 35.36 (30.30) Prunus serotina 17.03 (23.80) 12.20 (24.16) 14.61 (22.72) Hamamelis virginiana 16.87 (26.32) 8.46 (19.49) 13.82 (22.70) Vaccinium corymbosum 10.47 (25.06) 4.65 (15.20) 7.56 (19.41) Nyssa sylvatica 5.06 (12.09) 9.36 (22.19) 7.21 (17.13) Cornus florida 3.70 (7.61) 2.49 (6.49) 3.10 (6.71) Fagus grandifolia 1.68 (3.96) 2.67 (6.58) 2.17 (5.15) Betula alleghaniensis 1.39 (4.81) 2.04 (7.08) 1.72 (5.94) Sassafras albidum 1.39 (4.81) 2.04 (7.08) 1.72 (5.94) Magnolia acuminata 1.28 (4.44) 0.22 (0.75) 0.74 (2.60) Quercus rubra 0.46 (1.60) 0.54 (1.88) 0.50 (1.74) Other shrub species 9.52 (5.19) 10.95 (2.27) 11.49 (3.73) Total 100 100 100
41 The third vegetation community type delineated in the Flatiron Lake Bog uplands is the beech-oak-red maple forest community with 9.2 ha. The dominant tree species in this community type are black cherry, red maple, sassafras, and yellow-poplar
(Liriodendron tulipifera L.) (Table 2.10). There are a total of 18 tree species in this community type, including tree-of-heaven, an invasive species from Asia. This vegetation community had an average of 490 (± 210.33) total stems per ha and an average total basal area of 34.15 (± 14.78) m² per ha (Table 2.10). Black cherry has the highest importance value in this vegetation community, with a value of 30.60 percent
(Table 2.11).
Table 2.10: Number of stems and basal area per ha for all tree species within the beech- oak-red maple forest vegetation community in Flatiron Lake Bog, Portage County, Ohio. Numbers in parenthesis indicate standard deviation from the mean of all sample plots in the community. * indicates an invasive species. Species Number of Stems/ha Basal Area (m²/ha) Acer rubrum 147.5 (99.31) 9.6890 (8.75) Acer saccharum 2.50 (11.18) 0.0544 (0.24) Ailanthus altissima* 2.50 (11.18) 0.0687 (0.31) Betula alleghaniensis 8.75 (28.42) 0.3490 (1.18) Carya glabra 3.75 (16.77) 0.1298 (0.58) Fagus grandifolia 5.00 (10.26) 0.4857 (1.26) Hamamelis virginiana 1.25 (5.59) 0.0117 (0.05) Liriodendron tulipifera 41.25 (122.55) 5.5519 (15.91) Magnolia acuminata 18.75 (32.32) 2.2151 (4.31) Nyssa sylvatica 8.75 (20.32) 0.2695 (0.65) Ostrya virginiana 7.50 (23.08) 0.2973 (0.83) Populus deltoides 1.25 (5.59) 0.0689 (0.31) Populus grandidentata 17.50 (61.83) 1.2655 (4.09) Prunus serotina 173.73 (196.60) 9.7811 (10.59) Quercus alba 2.50 (7.69) 0.2848 (1.08) Quercus rubra 5.00 (13.08) 0.8105 (2.39) Sassafras albidum 38.75 (54.09) 2.7730 (4.39) Ulmus americana 3.75 (9.16) 0.0463 (0.12) Total 490.00 (210.33) 34.1523 (14.78)
42 Table 2.11: Relative density, relative dominance, and importance values for all tree species within the beech-oak-red maple forest vegetation community in Flatiron Lake Bog, Portage County, Ohio. Numbers in parenthesis indicate standard deviation from the mean of all sample plots in the community. * indicates an invasive species. Relative Relative Importance Species Density Dominance Value (%) Prunus serotina 32.07 (24.59) 29.12 (28.21) 30.60 (25.86) Acer rubrum 34.25 (20.90) 29.85 (25.22) 29.85 (22.27) Sassafras albidum 8.93 (14.11) 10.68 (20.00) 9.81 (16.81) Liriodendron tulipifera 7.27 (19.95) 11.84 (24.14) 9.56 (21.79) Magnolia acuminata 4.36 (7.97) 5.98 (12.15) 5.17 (10.01) Populus grandidentata 2.49 (7.88) 3.70 (11.16) 3.09 (9.51) Quercus rubra 1.27 (3.26) 2.53 (7.94) 1.89 (5.28) Fagus grandifolia 1.49 (3.22) 1.43 (3.65) 1.46 (3.21) Nyssa sylvatica 1.75 (4.15) 1.09 (2.49) 1.42 (3.23) Betula alleghaniensis 1.46 (4.75) 1.06 (3.85) 1.26 (4.30) Ostrya virginiana 1.41 (4.01) 0.85 (2.51) 1.13 (3.24) Ulmus americana 1.04 (2.64) 0.17 (0.43) 0.61 (1.52) Quercus alba 0.53 (1.62) 0.61 (2.33) 0.57 (1.88) Carya glabra 0.63 (2.80) 0.43 (1.92) 0.53 (2.36) Ailanthus altissima* 0.45 (2.03) 0.25 (1.11) 0.35 (1.57) Populus deltoides 0.14 (0.64) 0.28 (1.24) 0.21 (0.94) Acer saccharum 0.31 (1.40) 0.11 (0.47) 0.21 (0.93) Hamamelis virginiana 0.15 (0.70) 0.02 (0.10) 0.08 (0.40) Total 100 100 100
The shrub and sapling layer of the beech-oak-red maple forest vegetation
community is dominated by wild grape (Vitis riparia Michx.), multiflora rose, and black
cherry. This community type had an average of 5,800 (± 5,981.16) stems per ha and 2.15
(± 2.18) m² basal area per ha (Table 2.12). The beech-oak-red maple vegetation
community had 30 shrub and sapling species, including three invasive shrub species.
Wild grape had the highest importance value (17.12 percent) followed by multiflora rose
(14.44 percent) (Table 2.13).
43 Table 2.12: Number of stems and basal area per ha for all shrub and sapling species within the beech-oak-red maple forest vegetation community in Flatiron Lake Bog, Portage County, Ohio. Other tree species include sassafras, American beech, bitternut hickory, American elm, black oak, and pignut hickory. Other shrub species include witch-hazel, buttonbush, gooseberry, elderberry, and American hornbeam. Numbers in parenthesis indicate standard deviation from the mean of all sample plots in the community. * indicates an invasive species. Species Number of Stems/ha Basal Area (m²/ha) Acer rubrum 80 (246.23) 0.0098 (0.03) Acer saccharum 280 (900.06) 0.1105 (0.46) Amelanchier spp. 120 (320.53) 0.0147 (0.04) Castanea dentata 80 (357.77) 0.0884 (0.40) Cornus alternifolia 20 (89.44) 0.0025 (0.01) Cornus florida 80 (209.26) 0.0295 (0.10) Fraxinus pennsylvanica 40 (123.12) 0.0049 (0.02) Ligustrum vulgare* 400 (1138.79) 0.0491 (0.14) Lindera benzoin 100 (314.56) 0.0123 (0.04) Liriodendron tulipifera 60 (268.33) 0.0147 (0.05) Lonicera maackii* 100 (314.56) 0.0123 (0.04) Magnolia acuminata 60 (268.33) 0.0270 (0.12) Malus spp. 200 (894.43) 0.0245 (0.11) Prunus serotina 500 (755.33) 0.7682 (1.67) Quercus rubra 20 (89.44) 0.0025 (0.01) Rubus allegeniensis 100 (255.47) 0.0123 (0.03) Rosa multiflora* 960 (1170.87) 0.1276 (0.14) Viburnum recognitum 1,880 (5981.16) 0.3485 (1.16) Vitis riparia 360 (517.48) 0.3805 (0.67) Other tree species 160 (456.99) 0.0368 (0.13) Other shrub species 200 (378.36) 0.0687 (0.20) Total 5,800 (5,981.16) 2.1452 (2.18)
44 Table 2.13: Relative density, relative dominance, and importance values for all shrub and sapling species within the beech-oak-red maple forest vegetation community in Flatiron Lake Bog, Portage County, Ohio. Other tree species include sassafras, American beech, bitternut hickory, American elm, black oak, and pignut hickory. Other shrub species include witch-hazel, buttonbush, gooseberry, elderberry, and American hornbeam. Numbers in parenthesis indicate standard deviation from the mean of all sample plots in the community. * indicates an invasive species. Relative Relative Importance Species Density Dominance Value (%) Vitis riparia 11.14 (18.90) 23.09 (35.31) 17.12 (26.4) Rosa multiflora* 17.71 (21.12) 11.16 (16.57) 14.44 (17.89) Prunus serotina 7.94 (12.94) 16.48 (28.16) 12.21 (19.42) Ligustrum vulgare* 8.27 (23.24) 7.77 (23.21) 8.02 (23.20) Viburnum recognitum 9.06 (26.38) 6.43 (19.94) 7.74 (22.91) Quercus rubra 5.00 (22.36) 5.00 (22.36) 5.00 (22.36) Castanea dentata 3.33 (14.91) 4.74 (21.18) 4.04 (18.05) Acer saccharum 4.78 (16.32) 1.84 (7.43) 3.31 (11.81) Lindera benzoin 4.17 (13.11) 2.02 (7.54) 3.09 (9.56) Liriodendron tulipifera 2.09 (6.48) 1.78 (5.74) 1.93 (6.08) Amelanchier spp. 2.01 (4.95) 1.82 (4.55) 1.92 (4.74) Rubus allegeniensis 1.92 (4.94) 1.42 (3.54) 1.67 (4.21) Cornus florida 1.84 (5.00) 1.46 (3.83) 1.65 (4.41) Malus spp. 2.08 (9.32) 0.89 (3.99) 1.49 (6.65) Magnolia acuminata 0.68 (3.05) 1.83 (8.20) 1.26 (5.62) Acer rubrum 1.48 (4.57) 0.99 (3.53) 1.23 (3.93) Fraxinus pennsylvanica 1.56 (5.00) 0.64 (2.49) 1.11 (3.38) Cornus alternifolia 1.67 (7.45) 0.45 (2.03) 1.06 (4.74) Lonicera maackii* 1.10 (3.68) 0.89 (3.45) 0.99 (3.53) Other tree species 7.36 (5.46) 6.97 (5.63) 7.16 (5.46) Other shrub species 4.81 (10.53) 2.33 (5.63) 3.57 (7.38) Total 100 100 100
The last upland vegetation community within Flatiron Lake Bog is an aspen
stand. This community type is dominated by bigtooth aspen (Populus grandidentata
Michx.) and consists of 1.2 ha. The aspen forest community has an average of 495.83 (±
207.62) stems per ha and 24.97 (± 13.7) m² basal area per ha (Table 2.14). There are a
total of 10 tree species within this community. Bigtooth aspen has the highest
45 importance value rating (43.86 percent) followed by red maple and black cherry (Table
2.15).
Table 2.14: Number of stems and basal area per ha for all tree species within the aspen forest vegetation community in Flatiron Lake Bog, Portage County, Ohio. Numbers in parenthesis indicate standard deviation from the mean of all sample plots in the community. Species Number of Stems/ha Basal Area (m²/ha) Acer rubrum 120.83 (79.71) 3.1191 (3.47) Liriodendron tulipifera 41.67 (71.88) 2.6402 (4.11) Populus deltoides 8.33 (12.91) 0.4856 (0.79) Populus grandidentata 170.83 (43.06) 11.5647 (7.83) Prunus mahaleb 8.33 (20.41) 0.0869 (0.21) Prunus serotina 66.67 (58.45) 3.3551 (4.95) Quercus rubra 20.83 (29.23) 1.8854 (3.89) Quercus velutina 4.17 (10.21) 0.0327 (0.08) Sassafras albidum 50.00 (35.36) 1.7413 (1.58) Ulmus americana 4.17 (10.21) 0.0570 (0.14) Total 495.83 (207.62) 24.9681 (13.70)
Table 2.15: Relative density, relative dominance, and importance values for all tree species within the aspen forest vegetation community in Flatiron Lake Bog, Portage County, Ohio. Numbers in parenthesis indicate standard deviation from the mean of all sample plots in the community. Relative Relative Importance Value Species Density Dominance (%) Populus grandidentata 40.03 (20.67) 47.68 (19.66) 43.86 (18.97) Acer rubrum 23.32 (13.03) 14.34 (18.26) 18.83 (14.65) Prunus serotina 12.16 (10.01) 11.62 (14.38) 11.89 (11.63) Sassafras albidum 9.27 (5.95) 7.86 (10.22) 8.57 (7.60) Liriodendron tulipifera 5.92 (9.42) 7.35 (11.72) 6.63 (10.28) Populus deltoides 3.13 (4.97) 5.42 (9.73) 4.28 (7.27) Quercus rubra 3.07 (3.73) 5.09 (10.63) 4.08 (6.14) Prunus mahaleb 1.52 (3.71) 0.24 (0.58) 0.87 (2.15) Ulmus americana 0.79 (1.94) 0.30 (0.72) 0.54 (1.33) Quercus velutina 0.79 (1.94) 0.10 (0.25) 0.45 (1.10) Total 100 100 100
The shrub and sapling layer of the aspen stand is dominated by red maple, bush
honeysuckle and black cherry. This community type had an average of 7,866.67 (±
46 6,600.2) stems per ha and 3.84 (± 1.19) m² basal area per ha (Table 2.16). The aspen vegetation community had 18 shrub and sapling species, including two invasive shrub species. Red maple had an importance value rating of 29.24 percent, followed by bush honeysuckle with 13.56 percent (Table 2.17).
Table 2.16: Stems and basal area per ha for all shrub and sapling species within the aspen forest vegetation community in Flatiron Lake Bog, Portage County, Ohio. Numbers in parenthesis indicate standard deviation from the mean of all sample plots in the community. * indicates an invasive species. Species Number of Stems/ha Basal Area (m²/ha) Acer rubrum 1,266.67 (1085.66) 1.0063 (0.70) Amelanchier spp. 666.67 (1632.99) 0.6709 (1.64) Cornus florida 66.67 (163.30) 0.2045 (0.50) Fagus grandifolia 133.33 (326.60) 0.0736 (0.18) Fraxinus pennsylvanica 333.33 (393.28) 0.1064 (0.19) Liriodendron tulipifera 66.67 (163.30) 0.0082 (0.02) Lonicera maackii* 3,133.33 (4868.95) 0.4450 (0.72) Malus spp. 133.33 (326.60) 0.0164 (0.04) Nyssa sylvatica 66.67 (163.30) 0.0736 (0.18) Prunus mahaleb 133.33 (326.60) 0.0164 (0.04) Prunus serotina 733.33 (1055.78) 0.8099 (1.13) Quercus alba 666.67 (163.30) 0.0082 (0.02) Quercus rubra 133.33 (206.56) 0.0818 (0.18) Rosa multiflora* 66.67 (163.30) 0.0082 (0.02) Sassafras albidum 200.00 (219.09) 0.1554 (0.22) Vaccinium corymbosum 66.67 (163.30) 0.0082 (0.02) Viburnum recognitum 533.33 (1121.90) 0.1309 (0.30) Vitis riparia 66.67 (163.30) 0.0082 (0.02) Total 7,866.67 (6,600.20) 3.8370 (1.19)
47 Table 2.17: Relative density, relative dominance, and importance values for all shrub and sapling species within the aspen forest vegetation community in Flatiron Lake Bog, Portage County, Ohio. Numbers in parenthesis indicate standard deviation from the mean of all sample plots in the community. * indicates an invasive species. Relative Relative Importance Value Species Density Dominance (%) Acer rubrum 13.67 (13.62) 34.81 (23.19) 29.24 (18.02) Lonicera maackii* 19.59 (30.86) 7.53 (11.75) 13.56 (21.30) Prunus serotina 9.13 (10.10) 17.11 (23.22) 13.11 (16.08) Amelanchier spp. 4.51 (11.03) 13.28 (25.17) 7.39 (18.10) Sassafras albidum 5.91 (7.08) 8.87 (13.50) 7.39 (10.10) Fraxinus pennsylvanica 10.20 (13.26) 3.48 (5.33) 6.84 (8.57) Quercus rubra 3.13 (4.97) 3.87 (8.87) 3.50 (6.63) Cornus florida 1.28 (3.14) 5.41 (13.25) 3.35 (8.20) Viburnum recognitum 3.93 (6.62) 2.53 (5.59) 3.23 (5.99) Prunus mahaleb 4.17 (10.21) 0.41 (1.02) 2.29 (5.61) Malus spp. 3.70 (9.07) 0.81 (1.99) 2.26 (5.53) Quercus alba 2.79 (6.80) 0.55 (1.36) 1.67 (4.08) Fagus grandifolia 1.28 (3.14) 1.95 (4.77) 1.62 (3.96) Vaccinium corymbosum 1.85 (4.54) 0.41 (1.00) 1.13 (2.77) Vitis riparia 1.85 (4.54) 0.41 (1.00) 1.13 (2.77) Nyssa sylvatica 0.45 (1.10) 1.13 (2.76) 0.79 (1.93) Rosa multiflora* 1.28 (3.14) 0.22 (0.53) 0.75 (1.84) Liriodendron tulipifera 1.28 (3.14) 0.22 (0.53) 0.75 (1.84) Total 100 100 100
The vegetation community type occupying the majority of the wetland area (8.7
ha) of Flatiron Lake Bog is the mixed shrub swamp vegetation type. This community
type is dominated by the shrub community rather than the tree layer as in the upland
forest communities. The mixed shrub swamp community tree layer, although a lesser
component than the shrubs and saplings, is dominated by red maple, blackgum (Nyssa
sylvatica Marsh.), and yellow birch. It has an average of 184.72 (± 204.75) stems per ha
and 6.42 (± 5.8) m² basal area per ha (Table 2.18). There are a total of four tree species
within this community. Red maple has the highest importance value rating (57.93
48 percent) followed by blackgum and yellow birch (Table 2.19). Pin oak (Quercus
palustris Münchh.) is the fourth species, and a small component of this community type.
Table 2.18: Number of stems and basal area per ha for all tree species within the mixed shrub swamp vegetation community in Flatiron Lake Bog, Portage County, Ohio. Numbers in parenthesis indicate standard deviation from the mean of all sample plots in the community. Species Number of Stems/ha Basal Area (m²/ha) Acer rubrum 77.78 (78.07) 3.3658 (3.72) Betula alleghaniensis 66.67 (120.96) 0.9821 (1.73) Nyssa sylvatica 38.89 (68.18) 1.9812 (3.41) Quercus palustris 1.39 (5.89) 0.0930 (0.39) Total 184.72 (204.75) 6.4221 (5.80)
Table 2.19: Relative density, relative dominance and importance values for all tree species within the mixed shrub swamp vegetation community in Flatiron Lake Bog, Portage County, Ohio. Numbers in parenthesis indicate standard deviation from the mean of all sample plots in the community. Relative Relative Importance Species Density Dominance Value (%) Acer rubrum 54.69 (35.80) 61.18 (37.57) 57.93 (36.28) Nyssa sylvatica 24.51 (30.20) 25.70 (32.77) 25.11 (31.40) Betula alleghaniensis 20.14 (22.40) 12.05 (14.68) 16.10 ( 18.07) Quercus palustris 0.56 (2.36) 0.89 (3.77) 0.72 (3.06) Total 100 100 100
The shrub and sapling layer of the mixed shrub swamp vegetation community is
dominated by highbush blueberry, yellow birch and blackberry. This community type
had an average of 27,488.89 (±33,715.43) stems per ha and 6.91 (± 5.11) m² basal area
per ha (Table 2.20). Highbush blueberry had an importance value of 55.95 percent,
followed by yellow birch with 18.68 percent (Table 2.21). The mixed shrub swamp vegetation community had 10 shrub and sapling species, none of which were invasive.
49 Table 2.20: Number of stems and basal area per ha for all shrub and sapling species within the mixed shrub swamp vegetation community in Flatiron Lake Bog, Portage County, Ohio. Numbers in parenthesis indicate standard deviation from the mean of all sample plots in the community. Species Number of Stems/ha Basal Area (m²/ha) Acer rubrum 88.89 (377.12) 0.0545 (0.23) Betula alleghaniensis 1,222.22 (1759.53) 2.6589 (3.90) Cephalanthus occidentalis 22.22 (94.28) 0.0245 (0.10) Decodon verticillatus 88.89 (377.12) 0.0327 (0.14) Ilex verticillatus 1,488.89 (3716.56) 0.2700 (0.69) Malus spp. 66.67 (205.80) 0.0082 (0.03) Nyssa sylvatica 266.67 (565.69) 0.1418 (0.42) Rubus allegheniensis 533.33 (1521.61) 0.0655 (0.19) Vaccinium corymbosum 23,644.44 (34755.45) 3.6215 (4.76) Viburnum prunifolium 66.67 (205.80) 0.0300 (0.12) Total 27,488.89 (33,715.43) 6.9076 (5.11)
Table 2.21: Relative density, relative dominance and importance values for all shrub and sapling species within the mixed shrub swamp vegetation community in Flatiron Lake Bog, Portage County, Ohio. Numbers in parenthesis indicate standard deviation from the mean of all sample plots in the community. Relative Relative Importance Species Density Dominance Value (%) Vaccinium corymbosum 66.94 (35.25) 44.96 (35.34) 55.95 (33.55) Betula alleghaniensis 8.59 (16.30) 28.76 (33.61) 18.68 (23.77) Rubus allegheniensis 12.79 (30.24) 12.79 (30.24) 12.79 (30.24) Ilex verticillatus 5.41 (12.96) 5.47 (12.72) 5.44 (12.58) Nyssa sylvatica 4.60 (11.22) 5.73 (12.52) 5.17 (11.59) Viburnum prunifolium 0.39 (1.24) 0.64 (2.45) 0.51 (1.83) Decodon verticillatus 0.43 (1.81) 0.54 (2.28) 0.48 (2.05) Acer rubrum 0.42 (1.78) 0.47 (1.99) 0.44 (1.88) Cephalanthus occidentalis 0.14 (0.57) 0.56 (2.38) 0.35 (1.48) Malus spp. 0.28 (0.93) 0.09 (0.25) 0.19 (0.58) Total 100 100 100
The second wetland vegetation community type is a buttonbush swamp which
consists of 2.4 ha. This community is also dominated by the shrub layer instead of the
tree layer, in which the only species recorded was red maple. There were an average of
12.5 (± 25) stems per ha and 0.24 (± 0.47) m² basal area per ha in this community type
50 (Table 2.22). Red maple, as the only tree species, had a 100 percent importance value
(Table 2.23).
Table 2.22: Number of stems and basal area per ha for all tree species within the buttonbush swamp vegetation community in Flatiron Lake Bog, Portage County, Ohio. Numbers in parenthesis indicate standard deviation from the mean of all sample plots in the community. Species Number of Stems/ha Basal Area (m²/ha) Acer rubrum 12.50 (25.00) 0.2359 (0.47) Total 12.50 (25.00) 0.2359 (0.47)
Table 2.23: Relative density, relative dominance and importance values for all tree species within the buttonbush swamp vegetation community in Flatiron Lake Bog, Portage County, Ohio. Numbers in parenthesis indicate standard deviation from the mean of all sample plots in the community. Relative Relative Species Density Dominance Importance Value (%) Acer rubrum 25.00 (50.00) 25.00 (50.00) 25.00 (50.00) Total 100 100 100
The shrub and sapling layer of the buttonbush swamp vegetation community is
dominated by buttonbush (Cephalanthus occidentalis L.) and black willow (Salix nigra
Marsh.). This community type had an average of 15,700 (± 15,796.62) stems per ha and
3.40 (± 3.48) m² basal area per ha (Table 2.24). Buttonbush had an importance value of
60.32 percent, and black willow had an importance value of 18.2 percent (Table 2.25).
This vegetation community had four shrub and sapling species, none of which were
invasive.
51 Table 2.24: Number of stems and basal area per ha for all shrub and sapling species within the buttonbush swamp vegetation community in Flatiron Lake Bog, Portage County, Ohio. Numbers in parenthesis indicate standard deviation from the mean of all sample plots in the community. Species Stems/ha Basal Area (m²/ha) Vaccinium corymbosum 1,200.00 (1,423.61) 0.1473 (0.17) Cephalanthus occidentalis 10,100.00 (16,301.74) 2.5158 (2.59) Salix nigra 4,100.00 (8,200.00) 0.6995 (1.40) Rhus vernix 300.00 (600.00) 0.0368 (0.07) Total 15,700.00 (15,796.62) 3.3993 (3.48)
Table 2.25: Relative density, relative dominance and importance values for all shrub and sapling species within the buttonbush swamp vegetation community in Flatiron Lake Bog, Portage County, Ohio. Numbers in parenthesis indicate standard deviation from the mean of all sample plots in the community. Relative Relative Importance Species Density Dominance Value (%) Cephalanthus occidentalis 49.29 (44.16) 71.34 (24.94) 60.32 (34.39) Salix nigra 23.98 (41.53) 12.42 (21.51) 18.20 (31.52) Vaccinium corymbosum 19.59 (26.70) 11.70 (17.50) 15.64 (22.09) Rhus vernix 7.14 (12.37) 4.54 (7.87) 5.84 (10.12) Total 100 100 100
The final vegetation community in Flatiron Lake Bog, and the community of the
highest management focus, is the tamarack-hardwood bog, which consists of 1.1 ha. The
tree layer of this community type is dominated by tamarack, with a small fraction of
hardwoods. There is an average of 112.5 (± 74.4) stems per ha and 2.52 (± 2.06) m²
basal area per ha (Table 2.26). Tamarack has the highest importance value at 51.74
percent, followed by red maple and yellow birch (Table 2.27).
52 Table 2.26: Number of stems and basal area per ha for all tree species within the tamarack-hardwood bog vegetation community in Flatiron Lake Bog, Portage County, Ohio. Numbers in parenthesis indicate standard deviation from the mean of all sample plots in the community. Species Number of Stems/ha Basal Area (m²/ha) Acer rubrum 21.88 (26.44) 0.4608 (0.88) Betula alleghaniensis 25.00 (40.09) 0.3747 (0.64) Larix laricina 56.25 (65.12) 1.5290 (1.77) Nyssa sylvatica 3.13 (8.84) 0.0365 (0.10) Quercus palustris 6.25 (17.68) 0.1152 (0.33) Total 112.50 (74.40) 2.5162 (2.06)
Table 2.27: Relative density, relative dominance and importance values for all tree species within the tamarack-hardwood bog vegetation community in Flatiron Lake Bog, Portage County, Ohio. Numbers in parenthesis indicate standard deviations from the mean of all sample plots in the community. Relative Relative Importance Species Density Dominance Value (%) Larix laricina 48.88 (45.29) 54.59 (46.43) 51.74 (45.41) Betula alleghaniensis 16.47 (28.88) 15.93 (30.14) 16.20 (29.44) Acer rubrum 16.52 (24.52) 11.40 (16.85) 13.96 (20.37) Quercus palustris 3.13 (8.84) 3.20 (9.06) 3.16 (8.95) Nyssa sylvatica 2.50 (7.07) 2.38 (6.73) 2.44 (6.90) Total 100 100 100
The shrub and sapling layer of the tamarack-hardwood bog vegetation community is dominated by highbush blueberry and winterberry (Ilex verticillatus (L.) Gray). This community type had an average of 28,050 (± 11,385.08) stems per ha and 8.01 (± 3.53) m² basal area per ha (Table 2.28). Highbush blueberry had an importance value of 58.51 percent, followed by winterberry and others (Table 2.29). This vegetation community had a total of 9 shrub and sapling species.
53 Table 2.28: Number of stems and basal area per ha for all shrub and sapling species within the tamarack-hardwood bog vegetation community in Flatiron Lake Bog, Portage County, Ohio. Numbers in parenthesis indicate standard deviation from the mean of all sample plots in the community. Species Number of Stems/ha Basal Area (m²/ha) Acer rubrum 150 (207.02) 0.3620 (0.56) Andromeda polifolia 900 (2,545.58) 0.1104 (0.31) Betula alleghaniensis 200 (370.33) 0.5154 (1.04) Decodon verticillatus 50 (141.42) 0.0061 (0.02) Ilex verticillata 6,400 (6,047.43) 2.4053 (2.88) Larix laricina 100 (282.84) 0.5584 (1.58) Malus spp. 200 (565.69) 0.0736 (0.21) Quercus palustris 50 (141.42) 0.0552 (0.16) Vaccinium corymbosum 20,000 (9,715.97) 3.9270 (2.04) Total 28,050 (11,385.08) 8.0135 (3.53)
Table 2.29: Relative density, relative dominance and importance values for all shrub and sapling species within the tamarack-hardwood bog vegetation community in Flatiron Lake Bog, Portage County, Ohio. Numbers in parenthesis indicate standard deviation from the mean of all sample plots in the community. Relative Relative Importance Species Density Dominance Value (%) Vaccinium corymbosum 66.12 (28.94) 50.89 (27.18) 58.51 (27.11) Ilex verticillata 18.42 (15.80) 22.74 (21.65) 20.58 (18.20) Andromeda polifolia 10.71 (30.30) 2.05 (5.79) 6.38 (18.04) Larix laricina 1.19 (3.37) 10.34 (29.25) 5.77 (16.31) Betula alleghaniensis 0.94 (1.86) 6.51 (12.07) 3.72 (6.92) Acer rubrum 0.46 (0.66) 4.62 (6.52) 2.54 (3.56) Malus spp. 1.25 (3.54) 1.56 (4.42) 1.41 (3.98) Quercus palustris 0.31 (0.88) 1.17 (3.31) 0.74 (2.01) Decodon verticillatus 0.60 (1.68) 0.11 (0.32) 0.35 (1.00) Total 100 100 100
These seven vegetation communities (Table 2.1) were then reclassified using
TNC’s Plant Communities of the Midwest for their management purposes. The mixed mesophytic forest, beech-oak-red maple forest, and the aspen forest vegetation
communities under Anderson (1982) are all reclassified using TNC’s community guide
as a northern mixed mesophytic forest (TNC database code CEGL005222). The oak-
hickory forest under Anderson is reclassified as a black oak-white oak-hickory forest 54 (TNC database code CEGL002076). The mixed shrub swamp is reclassified as a
highbush blueberry poor fen (TNC database code CEGL005085), and the buttonbush
shrub swamp as a northern buttonbush swamp (TNC database code CEGL002190).
Finally, the tamarack-hardwood bog is reclassified as a central tamarack poor swamp
(TNC database code CEGL002472).
Peat Profiles
The peat resource was characterized along a 100 m transect from the open water
portion of Flatiron Lake Bog to the interior edge of the lagg (the lagg area itself was not
analyzed due to ponded water, increasing the potential for a mixing of horizons during
extraction). The von Post scale of humification (Table 2.30) was used to determine the
stage of decomposition of the peat within five profiles along this transect, and to determine changes with depth in the peat resource. Each distinct layer in these profiles
was given a unique sample ID code (Table 2.31).
The first peat sample in this transect was taken at the interior edge of the shrubs
surrounding the open water of Flatiron (0 m). For these samples, the peat was analyzed
to a minimum depth of 70 cm, depending on the water level and amount and depth of
roots. All of the peat within this first profile was determined to be one horizon (sample
ID 0A, Figure 2.5), with the von Post degree of humification as an H2, slightly
undecomposed. This first profile had high amounts of roots, and water filled the
sampling hole in under a minute.
55 Table 2.30: Characteristics for the different stages of decomposition using the von Post Degrees of Humification scale (von Post and Granlund 1926). von Post Scale Water/Peat Peat Degree of Plant Remains Released when Decomposition Humification Squeezed Completely H1 Easily Identified Clear Undecomposed Almost Completely H2 Easily Identified Clear/Yellowish Undecomposed Very Slightly H3 Identifiable Muddy Brown Decomposed Slightly H4 Slightly Pasty Very dark Muddy Decomposed Moderately Very Muddy with H5 Indistinct Structure Decomposed Peat Moderately- Structure More H6 Strongly Distinct After 1/3 Peat Released Decomposed Squeezing Strongly Faintly H7 1/2 Peat Released Decomposed Recognizable Very Strongly Dry Indistinct H8 2/3 Peat Released Decomposed Structure Almost Fully Very Little Almost all Peat H9 Decomposed Recognizable Released Completely All Wet Peat H10 None Discernible Decomposed Released
The second profile was completed at a distance of 20 m from the shrub edge surrounding the open water bog. This profile had three different horizons of peat (Figure
2.5). The first was from 0 (ground level) to 14 cm in the profile (sample ID 20a), and had a degree of humification of H2. The second was from 14 cm to 20 cm (sample ID 20b), and had a degree of humification of H5, moderately decomposed. The third (sample ID
20c) was at the depth of 20 to 80 cm and had a degree of humification of H4, slightly decomposed peat.
The third profile was sampled at a distance of 40 m from the edge of the shrub layer surrounding the open water, and also had three distinct horizons of peat (Figure 56 2.5). The first was to a depth of 15 cm from ground level (sample ID 40a), and had the degree of humification of H2. The second was from 15 cm to 27 cm (sample ID 40b), and had the degree of humification of H5. Finally, the third horizon was from 27 to 108 cm (sample ID 40c) and also had a degree of humification of H5, but was slightly less decomposed than the second horizon, bordering on the H4 degree of humification but with more overall properties of the H5 stage.
The fourth profile was at a distance of 60 m from the shrub edge surrounding the open water, and had a total of three distinct horizons in the peat (Figure 2.5). The first was from 0 (ground level) to 22 cm in the profile depth (sample ID 60a), and had a degree of humification of H2. The second was from 22 to 51 cm (sample ID 60b), and had a degree of humification of H4. The final horizon was from 51 to 100 cm (sample ID
60c) and had the degree of humification of H6, moderately-strongly decomposed peat.
The fifth profile was at a distance of 80 m from the shrub edge surrounding the
Flatiron Lake, and also had three distinct peat horizons (Figure 2.5). The first horizon was from 0 (ground level) to 17 cm (sample ID 80a), and had a degree of humification of
H4. The second horizon was from 17 to 37 cm (sample ID 80b), and had a degree of humification of H6. The third horizon was from 37 to 100 cm (sample ID 80c), and had a degree of humification of H9, practically fully decomposed peat, the highest level of decomposition in the entire transect.
The final profile in the transect was taken at 100 m from the shrub edge of the lake, which was also the interior edge of the lagg ecotone. This profile also had three distinct peat horizons (Figure 2.5). The first was from 0 to 17 cm (sample ID 100a), with the degree of humification of H3. The second was from 17 to 40 (sample ID 100b), with
57 the degree of humification of H6. The final horizon was from 40 to 102 cm (sample ID
100c), and had a degree of humification of H9, similar to the previous profile.
Table 2.31: Sample ID codes for each distinct layer in the peat profiles from Flatiron Lake Bog, Portage County, Ohio.
Sample ID Distance from shrub edge (m) Depth (cm) 0a 0 0-70 20a 20 0-14 20b 20 14-20 20c 20 20-80 40a 40 0-15 40b 40 15-27 40c 40 27-108 60a 60 0-22 60b 60 22-51 60c 60 51-100 80a 80 0-17 80b 80 17-37 80c 80 37-100 100a 100 0-17 100b 100 17-40 100c 100 40-102
58
Figure 2.5: von Post (1926) scale of humification for layers within the peat profiles taken from Flatiron Lake Bog, Portage County, Ohio.
Wetland Delineation
The wetland complex surrounding the bog itself was delineated using the U.S.
Army Corp of Engineers Wetland Delineation Manual. All of the sample sites delineated as within the wetland boundary were found to have at least 50 percent hydrophytic vegetation, hydric soils, and hydrology of either water at the surface or within 12 in
(30.48 cm) of the surface, following the guidelines established by the U.S. Army Corp of
Engineers Wetland Delineation Manual. Several delineation sites within the wetland boundary also had redoxymorphic features (mottling) present in areas of lower water levels, indicating that water levels fluctuate and are higher during some seasons of the year than when sampled. Delineation for this study occurred during summer with full vegetation and high evapotranspiration rates, resulting in lower water levels than are present during other seasons of the year. 59 In the sample units located in the transition zone between the wetland and the
upland, 25 of the 78 sample locations were determined to be within the wetland
boundary. These 25 samples had at least 50 percent hydrophytic vegetation, hydric soils,
and water or water indicators within 30.48 cm of the soil surface. Of the other 53 samples, four did not meet the vegetation requirement of 50 percent or greater of
hydrophytic plants, 53 did not meet the hydrology requirements of water or water indicators within 30.48 cm of the surface, and six did not have hydric soils. These
samples from the center of the delineation transects were primarily used in the actual
determination of the boundary. Those that met all three requirements, and where the upland edge samples did not meet all three, were taken as the boundary, and for those that
did not meet the requirements, the sample unit on the interior (wetland edge) of the
transect was used as the wetland boundary delineation point. The sample units in the
upland portions of the wetland delineation were nearly all located outside of the wetland
boundary. Only two of these samples met the three wetland requirements, and in these
two cases, were used as the delineation point for the wetland boundary (Figure 2.6).
Two sample points for the wetland delineation were considered outliers when the wetland boundary was mapped using ArcGIS (Figure 2.6). One point was located within
the wetland a distance from the boundary, and is believed to be an error in the recording
of the GPS coordinates. The other “outlier” is a point in the southwest corner that is
actually a small extension of the wetland to the west in a narrow area.
The eastern wetland area located in the Flatiron Lake Bog landholding was outlined by taking GPS points every 20 m along the edge. No wetland delineation was
60 conducted in this area due to the distinct rise in elevation separating the wetland from the upland along the entire wetland boundary.
Figure 2.6: Wetland boundary determined by delineation transects and the U.S. Army Corp of Engineers Wetland Delineation Manual in Flatiron Lake Bog, Portage County, Ohio.
Tree Core Analysis
Tree cores were taken from four areas immediately surrounding the bog in the four cardinal directions. Cores were also taken from the small area of tamaracks located in the southern portion of the wetland complex in order to compare establishment dates between these two areas. Many of the trees in this southern sampling unit were found to be rotten in the center, which limited the number of useable samples that could be taken.
A total of 33 tree cores were taken in the central bog area, and four solid cores were taken
61 from the southern wetland area. The trees sampled ranged from 5.9 to 36.3 cm dbh
(Table 2.32), and cores were taken at a height of 25 cm from the ground.
The sampled trees at Flatiron Lake Bog ranged in age from 30 to 124 years (Table
2.33). The four tamaracks sampled in the southern area of the wetland were all established in the early 1900s, between 1910 and the 1930s (Figure 2.7). The high percentage of rotting trees in this location, the ages of the successfully cored trees, and the lack of regeneration of tamaracks in this area indicate that this species of tree will not continue.
Of the trees sampled in the area immediately surrounding the open water, establishment dates ranged from 1883 to 1977 (Figure 2.8). Tamarack ranged across this entire gradient, with the highest period of recruitment during the 1910s to the 1930s, similar to that of the tamaracks located in the southern wetland area (Figure 2.9). The red maples established between the 1910s and the 1960s (Figure 2.9). The yellow birch were established between the 1950s and 1970s, with the smallest range of recruitment, and later than the other two species (Figure 2.9).
62 Table 2.32: Species and diameters (DBH) of cored trees from the Flatiron Lake Bog wetland complex. Tree ID Species DBH FL5101T Larix laricina 10.8 FL5102T Larix laricina 15.5 FL5103T Larix laricina 17.5 FL5104B Betula alleghaniensis 11.9 FL5105T Larix laricina 27.7 FL5106M Acer rubrum 21.2 FL5107M Acer rubrum 8.8 FL51a01T Larix laricina 13.2 FL51a02T Larix laricina 7.2 FL51a03T Larix laricina 11.4 FL51a04T Larix laricina 19.4 FL51a05T Larix laricina 8.1 FL51a06B Betula alleghaniensis 8 FL51a07M Acer rubrum 8.5 FL51a08T Larix laricina 36.3 FL51a09T Larix laricina 18.1 FL5201T Larix laricina 13.3 FL5202B Betula alleghaniensis 16.9 FL5203T Larix laricina 26.9 FL5204T Larix laricina 19.1 FL5205M Acer rubrum 27.8 FL5206T Larix laricina 19.5 FL5207T Larix laricina 10.8 FL5208T Larix laricina 22.9 FL5209T Larix laricina 16.4 FL5210T Larix laricina 26 FL5211B Betula alleghaniensis 16.4 FL52a01T Larix laricina 11.4 FL52a02T Larix laricina 22.4 FL52a03T Larix laricina 14.2 FL52a04T Larix laricina 19.5 FL52a05T Larix laricina 5.9 FL52a06T Larix laricina 21.5 FLS01 Larix laricina 14.3 FLS02 Larix laricina 16.4 FLS03 Larix laricina 25.7 FLS04 Larix laricina 28.5
63 Table 2.33: Species, ages, and estimated establishment dates for all trees cored within Flatiron Lake Bog, Portage County, Ohio. Tree ID Species Age Establishment Year FL5101T Tamarack 37 1970 FL5102T Tamarack 73 1934 FL5103T Tamarack 101 1906 FL5104B Yellow Birch 57 1950 FL5105T Tamarack 82 1925 FL5106M Red Maple 73 1934 FL5107M Red Maple 39 1968 FL51a01T Tamarack 79 1928 FL51a02T Tamarack 69 1938 FL51a03T Tamarack 69 1938 FL51a04T Tamarack 91 1916 FL51A05T Tamarack 91 1916 FL51A06B Yellow Birch 30 1977 FL51A07M Red Maple 38 1969 FL51A08T Tamarack 124 1883 FL51A09T Tamarack 119 1888 FL5201T Tamarack 73 1934 FL5202B Yellow Birch 36 1971 FL5203T Tamarack 84 1923 FL5204T Tamarack 78 1929 FL5205M Red Maple 93 1914 FL5206T Tamarack 80 1927 FL5207T Tamarack 39 1968 FL5208T Tamarack 107 1900 FL5209T Tamarack 95 1912 FL5210T Tamarack 92 1915 FL5211B Yellow Birch 38 1969 FL52a01T Tamarack 81 1926 FL52a02T Tamarack 96 1911 FL52a03T Tamarack 80 1927 FL52a04T Tamarack 94 1913 FL52a05T Tamarack 78 1929 FL52a06T Tamarack 85 1922 FL501 Tamarack 95 1912 FL502 Tamarack 76 1931 FL503 Tamarack 78 1929 FL504 Tamarack 80 1927
64
Figure 2.7: Decades of establishment for tamaracks located in the southern portion of the wetland area within Flatiron Lake Bog, Portage County, Ohio.
Figure 2.8: Decades of establishment for all trees located in the area surrounding the open water lake of Flatiron Lake Bog, Portage County, Ohio.
65
Figure 2.9: Decades of establishment by species for sampled trees surrounding the open water lake portion of Flatiron Lake Bog, Portage County, Ohio. Black bars indicate tamarack, gray bars indicate red maple, and white bars indicate yellow birch.
Years in which trees were released were also determined from these cores. The majority of releases found occurred in the 1920s, 1950s, and 1980s (Figure 2.10). Red maples, on a percentage basis, experienced more releases than tamarack or yellow birch.
Seventy-five percent of the red maples cored had at least one release from establishment to the present (Figure 2.11). Fifty-nine percent of all tamaracks (Figure 2.12) and 50 percent of the yellow birch (Figure 2.13) cored experienced at least one release.
66
Figure 2.10: Release years for all trees cored at Flatiron Lake Bog, Portage County, Ohio.
Figure 2.11: Release years for all red maple cored at Flatiron Lake Bog, Portage County, Ohio.
67
Figure 2.12: Release years for all tamarack cored at Flatiron Lake Bog, Portage County, Ohio.
Figure 2.13: Release years for all yellow birch cored at Flatiron Lake Bog, Portage County, Ohio.
2.4 Discussion
All seven of the vegetation communities delineated within Flatiron Lake Bog require different management actions to maintain the current or desired conditions.
Invasive species are a concern within three of the four upland vegetation communities.
68 One of the main goals of TNC is to maintain the natural biodiversity of the areas under its protection. The presence of these non-native invasive species is a concern that needs addressed in the landholding to help maintain this specific goal. Invasive species recorded during this study include: multiflora rose, bush honeysuckle, privet, glossy buckthorn, tree-of-heaven and garlic mustard. The species of highest concern at this time are the tree-of-heaven and garlic mustard. Privet, glossy buckthorn and honeysuckle are present in smaller abundances, and as a result, are not as high on the management priority list. It is expected that as the canopy closes more in these vegetation communities that the multiflora rose will begin to die out, lessening the need for physical removal of this species. The honeysuckle was only found in areas with high canopy closure, which may be the reason for the lower density, as this species is found more often along edges with higher light.
Another species that may be considered invasive (although native) in two of these vegetation communities is red maple. This species was present with high importance values in all of the communities, and in most of these communities also dominated the regeneration. This primarily causes concerns within the oak-hickory forest vegetation community, where red maple seedlings and saplings compete with the desired oak and hickory regeneration (Abrams 2005), and in the tamarack-hardwood bog, where it could potentially dry out the upper peat layer through increased transpiration (Charman 2002,
Hutnick and Yawney 1961).
Each of these communities also has different stand characteristics, implying past disturbance histories, and will require different management plans to achieve the desired condition. Several areas of the mixed mesophytic and beech-oak-red maple vegetation
69 communities show evidence of past logging and clearing in the form of stumps, small openings of younger trees and denser shrubs, and in the species composition itself. Black cherry and yellow-poplar are shade intolerant species that generally regenerate following periods of high disturbance where the canopy is significantly opened allowing high levels of light to hit the forest floor. These areas are along the perimeter of the Flatiron Lake
Bog property and also in the areas that were cleared for the proposed mining that was never carried out. The species composition in these community types will most likely shift in the future to more shade-tolerant species such as sugar maple and beech.
The oak-hickory forest shows little signs of major past disturbance, with only a few older stumps evident. This area also currently has no invasive species, and efforts are proactively undertaken by TNC in these areas to stop the encroachment of these species into the area. Since this vegetation community is primarily located on the upland peninsula within the wetland complex, a natural boundary is formed around much of the area, and only the small portion of land connecting this peninsula with the remainder of the uplands is a concern for the spread of invasive species.
This community, however, is not regenerating with the current canopy species. If this community type is desired in the future, efforts will be needed to encourage the regeneration of the current oak and hickory species, and to discourage the regeneration present of other species, particularly red maple. This community type is smaller than most managed oak-hickory forests, which may limit the management options available for maintaining this community composition. Current studies by the USDA Forest
Service, Ohio Department of Natural Resources, and The Ohio State University are showing the effectiveness of shelterwood harvests and prescribed fire in regenerating
70 oaks, but these practices are not very feasible in small land areas such as this community.
It may be necessary to allow succession to change the composition of this stand to a more mesic-type forest than currently exists, despite the goal of maintaining the natural biodiversity of the landholding.
The wetland vegetation communities may also change over time. Runoff from adjacent agricultural fields is entering the northwest area of the wetland, and with the
increased nutrient inflow as a result of this, species composition may, over a period of
time, become more diverse. This northwest corner of the wetland already has a different
species composition and structure than the other community types, with more shrub and
herbaceous than trees. This area is the buttonbush shrub swamp community, with species
not found in the other community types.
Over time, this nutrient inflow may alter the tamarack-hardwood bog community
type, and increasing competition for the species adapted to the nutrient-poor conditions
currently present. These are the species of highest concern to TNC, including pitcher-
plants, round sundew, and orchids. This concern, combined with the natural succession
pattern of kettle-hole bogs and the threats presented by global warming, could result in
the overall loss of the community type.
The natural succession pattern that is seen in these peatland types include the
open water lake stage as is present here, to one without a lake and its concentric zones of
vegetation. Eventually, the kettle-hole bog will become covered over with Sphagnum
and shrubs. This in itself could result in the loss or reduction of the rare bog-dependent
species.
71 Global warming poses more threats than have been considered in past kettle-hole
bog management. With the potential for increasing temperatures, natural succession may
occur at a faster rate than historically, speeding the transition from a lake and zonation
vegetation to a more consistent vegetation species composition across the wetland complex (Ashcroft et al. 2009). Global warming may also have the ability to alter the amount of rainfall received by the area over time. Increased rainfall may help limit impacts of increasing temperatures to some degree, but decreasing amounts of rainfall could have an additive effect to the increasing temperatures. Evapotranspiration rates will increase as the peat layer dries out and the presence and density of vascular plants increase, further increasing the rates of succession in the bog.
The tree cores taken from the tamarack-hardwood bog community indicate that the tamaracks are still surviving and regenerating in this community. Based on the establishment dates determined from the tamarack cores, and the presence of seedlings and saplings in the vegetation community sample plots, this species is not in any immediate danger of being displaced. Red maples and yellow birch seem to have established later than the tamaracks, but results from these two species are based on a very small sample population and may not accurately reflect the entire range of establishment dates.
The releases that were determined from these cores have implications for future succession. Red maple and yellow birch individuals appear to have more recent releases than the tamaracks. Most of the tamarack releases were prior to 1950, whereas all of the releases for the other two species occurred after 1950. This may indicate that these two species are better able to respond to conditions allowing a release than the tamaracks, and
72 may use the limited available nutrients when they become available more quickly. The
implications in these findings are not as positive as the knowledge that the tamaracks are
present and regenerating. Although this species is still the dominant tree species, the
maples and birches may increase in the future due to their ability to respond to release.
This is further enhanced in that the regeneration of red maple and yellow birch is also
present at a higher combined importance value (percentage) than the tamarack
regeneration in the tamarack-hardwood bog.
2.5 Management Implications
Non-native invasive species should be a high priority issue within Flatiron Lake
Bog. Efforts are currently undertaken by TNC to control garlic mustard, but the species is still prevalent all areas of the upland forest understory except for the oak-hickory
forest. This community type needs to be consistently monitored to keep garlic mustard
out of the area. All other community types should have this species pulled or sprayed
repeatedly for several years to attempt to eradicate it.
The tree-of-heaven within the property also needs eradicated. Several larger individuals are present, which have been producing seed. These need removed, and the tree-of-heaven seedlings and saplings need to be killed either through hand-pulling or
through the use of pesticides. This species was found in several areas of Flatiron,
including one area along a portion of the wetland boundary.
Both garlic mustard and tree-of-heaven will need monitored and removed for
several years, since both species are present in the seedbank. Tree-of-heaven will also
resprout if cut, so if these are not treated with herbicide or the herbicide is ineffective
73 after the first application, the sprouts will also need removed for several years following
the initial removal.
While multiflora rose is prevalent throughout the majority of the uplands, this
species does not do well in closed-canopy conditions. This reduces the immediate
concern for control of the species, and action may only need to be taken if it does not die
out as the canopy closes over. Bush honeysuckle and privet were found in small densities
throughout the landholding and may be the least important invasive species issue to manage for at this time. If there is adequate time for their removal, they should be
removed, but should be low on the priority list for eradication.
The runoff currently entering the wetland complex may need to be diverted
around the wetland to reduce the nutrient inflow into the bog community. Erosion
barriers had been installed previously by TNC to reduce rates and sediment entering, but
have fallen apart in most places since installation. The replacement of these devices is a
necessary action to reduce the amount of nutrients entering the wetland complex.
If the oak-hickory vegetation community is a desired component of Flatiron Lake
Bog in the future, management of the area to establish advanced regeneration of the oak
and hickory species is needed. This may require the removal of some of the overstory
trees to allow higher light levels on the forest floor, although the control of non-desired
species will be necessary prior to their removal to aid in the establishment of oaks. The
size of this community will limit the management actions that can feasibly be undertaken,
however.
74 2.6 Conclusions
Flatiron Lake Bog, owned and managed by TNC, is a diverse property with several features that warrant the protection of the area. The kettle-hole bog, one of only three relatively undisturbed of its kind remaining in the state of Ohio, is a community of uniquely adapted vegetation species and is a community present at the extreme southern end of its range. TNC desires to maintain the natural biodiversity and ecologically important features present on this site, and this research provides a basic framework on which to build an effective management plan. While some of the desired species or even communities face threats that may eventually warrant their loss or transition to other community types, several management options are available to attempt to achieve the overall desired outcomes.
This study also provides the basic methodology and recommendations that may be used in the other kettle-hole bog communities present in Ohio. Many of the threats that Flatiron Lake Bog is facing are threats to these other ecosystems, and the results determined in this study may be applicable in the other kettle-hole bogs in the state to help maintain their natural biodiversity, recognize threats that are present, and in determining the most effective ways to manage these ecosystems.
More detailed information is needed to fully manage and maintain these ecosystems, however. The interactions that occur between the bog and the groundwater would allow for a better assessment of the potential impacts of global warming. A better understanding of necessary buffers to limit impacts that can be created by changing land uses surrounding these areas could reduce problems in the future with runoff and other nutrient additions. All of the results determined in this research project and in future
75 projects will also provide a greater overall understanding of kettle-hole bogs, and can provide tools for the future conservation and management of these unique ecosystems.
76
CHAPTER 3
CHANGES IN VEGETATION AND WATER CHEMISTRY TO FLATIRON LAKE BOG WITH CHANGING LAND USES OVER A 24-YEAR PERIOD
3.1 Introduction
Throughout the world bogs are found primarily in the boreal and cool temperate
regions of the world (Moore 2002). Bogs are wetland types that accumulate organic
material (peat), have acidic water and substrate, and are exclusively or primarily
precipitation fed (Moore 2002, Butovsky et al. 2004, Nordbakken et al. 2003). Due to
the nature of the water source and its isolation from the groundwater, bogs are nutrient-
poor wetland types, and support a unique flora composition. Sphagnum mosses are often
the most defining plant species in these ecosystems and their characteristics help
perpetuate the acidic, nutrient-poor water chemistry (Rochefort and Vitt 1990). Due to
these conditions, bogs often support populations of rare plant species, whether on a local,
regional or global scale (Topic and Stancic 2006, Butovsky et al. 2004).
Historically, the anthropogenic view of bogs has been utilitarian in nature (Mitsch
and Gosselink 2007). On the global scale, bogs have been areas of high conversion to
agricultural uses due to the high amounts of organic material, which after drainage results in productive farm land. Peat has been and still is used as a source of fuel in many areas, and Sphagnum mosses are harvested for horticultural purposes. Throughout the past
77 century, however, focus in bog ecosystems has shifted slowly to a more conservation-
based mindset (Butovsky et al. 2004, Topic and Stancic 2006, Tiemeyer et al. 2006).
Throughout the nineteenth and early twentieth centuries, Ohio peatlands were seen primarily as a resource for peat and sphagnum and as productive agricultural land once drained (Dachnowski 1912). Alfred Dachnowski’s Geological Survey of Ohio publication entitled Peat Deposits of Ohio: Their origin, formation, and uses (1912) is a survey of the location and quality of peatlands across the state. After the name of each peatland surveyed, a description of its location, size, quality of peat as a fuel, and potential productivity of the land if used for agriculture is listed. This publication clearly outlines the prevailing view of the importance of peatland utilization during this time period.
More recently the focus has changed from how to best utilize and exploit peatlands, to more of an emphasis on how to conserve and protect these ecosystem types
(Tomassen et al. 2004). One example of this changing paradigm with respect to bog ecosystems is in Ohio. It is estimated that only four percent of the state’s original peatlands remain and support the typical vegetation of the ecosystem type (Andreas and
Knoop 1992). There are currently only three relatively undisturbed kettle-hole bogs left in Ohio, all of these under some sort of protection (Andreas and Bryant 1990). Flatiron
Lake Bog, located in southwest Portage County, is owned and protected by The Nature
Conservancy (TNC) and is closed to all public admittance. Fern Lake Bog, in Geauga
County, is a Cleveland Museum of Natural History Natural Area with limited access to the public (Cleveland Museum of Natural History http://www.cmnh.org/site/Conservation_NaturalAreas_Map_FernLakeBog.aspx. March
78 31, 2009). Triangle Lake Bog, in Portage County, is the third relatively undisturbed kettle-hole bog in Ohio and is owned by the Ohio Department of Natural Resources
Division of Natural Areas and Preserves. This bog is open to the public, but has boardwalks installed to limit human impacts (ODNR Division of Natural Areas and
Preserves http://www.dnr.state.oh.us/location/triangle/tabid/967/Default.aspx. March 31,
2009).
One of the more serious threats facing these Ohio relic kettle-hole bogs are changing land uses. Although bogs are naturally isolated ecosystems, with no or very little interaction between the surface and groundwater, changes in adjacent land uses and the loss of natural vegetation buffers surrounding these bogs can potentially change this isolation. Prior to human settlement, the land cover type surrounding all three of these
bogs was forestland. Currently, the surrounding land uses range from gravel mining to
agriculture to suburban development. Agricultural runoff affects the water chemistry in
these bogs (Andreas and Bryan 1990), which may be altering the water chemistry and in
turn, the vegetation composition of the bogs as well.
Flatiron Lake Bog, Fern Lake Bog, and Triangle Lake Bog were studied in the
1980’s by Andreas and Bryan (1990) from Kent State University to characterize their
vegetation and water chemistry. The main goals of their study were to characterize the
vegetation and water chemistry of these three bogs and to compare them with similar
bogs of other regions within the United States. This study, undertaken at Flatiron Lake
Bog, consists of several key parts, beginning with an assessment of changes to the bog’s
vegetation (species composition and structure) and water chemistry characteristics over
the 24 years since the study by Andreas and Bryan (1990) was undertaken. These
79 changes are compared with changes in adjacent land uses and the continued inflow of
agricultural runoff from the adjacent farm lands surrounding the Flatiron Lake Bog
landholding.
3.2 Methods
Study Area Description
Flatiron Lake Bog is located in the southwestern corner of Portage County, Ohio
(N 41˚ 2’; W 81˚ 22’) and is one of the three remaining relatively undisturbed kettle-hole
bogs in Ohio. TNC currently owns this bog, its surrounding wetland complex, and an area of uplands surrounding this complex (Figure 3.1). The entire landholding is 39.2
hectares. The area is not open to the public due to the sensitive nature of the Sphagnum
mat and the potential damage that can be caused by human disturbances.
Figure 3.1: Aerial photo and boundary of the Flatiron Lake landholding (map created by TNC August 18, 2004). 80 The bog is located within the Little Cuyahoga River watershed (Subwatershed number 04110002-030-050), which ultimately drains north into Lake Erie
(http://www.oh.nrcs.usda.gov/technical/14-digit/14narr04110002.html, accessed April 2,
2009). This watershed drains 4773.7 ha, from below the Mogadore Reservoir (Portage
County, Ohio) to the Springfield Lake outlet (Summit County, Ohio). The Flatiron Lake
Bog landholding constitutes 0.7 percent of the Little Cuyahoga watershed.
This bog is representative of the concentric zones of vegetation typical of this type of kettle-hole bog in the open water lake successional stage. The open water area is surrounded by a floating Sphagnum mat with swamp loosestrife (Decodon verticillatus
(L.) Elliot), sundew (Drosera rotundifolia L.) and pitcher-plants (Sarracenia purpurea
L.) interspersed on the higher hummocks of the area. Surrounding the mat is a layer of
shrubs (primarily swamp loosestrife, highbush blueberry (Vaccinium corymbosum L.), and huckleberry (Gaylussacia baccata (Wangenh.) K. Koch) with a ground layer of
Sphagnum, sundew, sedges (Carex spp.), pitcher plants, and other herbaceous species.
Outside of the shrub zone is a ring of tamaracks (Larix laricina (Du Roi) K. Koch), yellow birch (Betula alleghaniensis Britton), and red maple (Acer rubrum L.). The tamarack trees are at the southernmost extreme of their natural distribution
(http://plants.usda.gov/java/profile accessed April 3, 2009).
The other areas of the wetland complex are a combination of two vegetation community types (Figure 3.2). The majority of the area is a mixed shrub swamp, dominated by blueberry shrubs and red maple and yellow birch. The other community type is a buttonbush shrub swamp, dominated by buttonbush (Cephalanthus occidentalis
81 L.) and black willow (Salix nigra Marsh.). This community type is located in the northern area where agricultural runoff is a direct influence on the water chemistry.
The uplands of Flatiron Lake Bog are characterized by several different
community types (Figure 3.2). These include a mixed mesophytic forest, a beech-oak-
red maple forest, an oak-hickory forest, and an aspen stand. The entire upland areas
owned by TNC are forested, although the uplands adjacent to their boundaries are not.
On the western boundary of Flatiron Lake Bog, agriculture (row crops) is the principle
land use. To the north of the boundary is residential land use, and to the east is a less
dense residential area with more forest cover than in the other three cardinal directions.
The southern area of the adjacent property was previously mined, and is currently a lake
where the gravel and sand was removed.
82
Figure 3.2: Vegetation communities of the Flatiron Lake Bog landholding.
83 The soil in the bog and surrounding wetland complex is Carlisle muck (euic, mesic, typic Medisaprists), which is a very poorly drained Histosol (USDA Soil
Conservation Service 1978). This soil series has moderately rapid permeability and high available water capacity. The soil series on the upland portions of the Flatiron Lake Bog landholding include Chili (fine-loamy, mixed, mesic, typic Hapludalf) silt loam, 2 to 6 percent slopes, Chili gravelly loam, 6 to 12 percent slopes that are moderately eroded,
Sebring silt loam (fine-silty, mixed, mesic, typic Ochraqualfs), Chili-Wooster (Wooster – fine-loamy, mixed, mesic, typic Fragiudalfs) complex, 6 to 12 percent, 12 to 18 percent, and 18 to 30 percent slopes, Chili-Oshtemo (Oshtemo – coarse-loamy, mixed, mesic, typic Hapludalfs) complex, 12 to 18 and 18 to 25 percent slopes, and gravel pits (Figure
2.2). The parent material of the area is glacial till deposits of the Kent Moraine, which consists of high amounts of gravel and was deposited by a succession of glaciers and glacial retreats, from approximately 40,000 years before present until 15,700 years before present (Andreas and Bryan 1990).
84
Figure 3.3: Soils of the Flatiron Lake Bog landholding (http://websoilsurvey.nrcs.usda.gov/app/WebSoilSurvey.aspx, accessed May 15, 2008).
Site History and Management Issues
Flatiron Lake Bog, the focus of this study, has had a diverse land use history
(personal communication, Adair June 6, 2007). The bog has been used by local residents
for at least several generations as a place to collect blueberries. One neighboring
landowner (personal communication, Brooker June 6, 2007) recalls a road that entered
into the Flatiron Lake Bog landholding that allowed people to enter the bog to harvest
blueberries, which was allowed by the owner at the time if one quart of blueberries was given as payment for every three or four quarts collected. These were then sold at a roadside stand to those who did not want to pick their own.
In the early-mid 1900’s, the area was planned to be mined for gravel and sand.
For a variety of reasons, and several versions currently are passed through the local lore, the mining operation was halted, saving the bog. Remnants of this planned operation are 85 still evident in scattered abandoned equipment, washing pits, and a retainment wall of logs.
Current threats to the bog are different than those that were faced in the past.
Invasive species are a major concern in the management of Flatiron Lake Bog. Garlic mustard (Alliaria petiolata (M. Bieb) Cavara & Grande), multiflora rose (Rosa multiflora
Thunb.), glossy buckthorn (Rhamnus frangula Mill.), autumn-olive (Elaeagnus umbellate
Thunb.), and tree-of-heaven (Ailanthus altissima (Mill.) Swingle) are all present in the upland areas of the landholding, and in many areas, these invasives dominate the upland understory of the forest communities. Accelerated woody encroachment (based on the results of this study) is also evident within the bog. While this is a natural occurrence in the succession of bogs, red maple is currently encroaching in the wetland complex, which may be problematic in this type of ecosystem. The transpiration rates associated with red maple may reduce the water levels in the wetlands, drying out the substrate and allowing for more red maples to colonize, creating a negative feedback loop (Charman 2002). The root systems of red maple in wetland ecosystems is shallow and spread out, allowing for the uptake, and therefore the transpiration, of high amounts of water from the surface area of the wetland (Hutnick and Yawney 1961).
Another management issue that Flatiron Lake Bog is facing is poaching of the rare bog plants. Pitcher plants, sundews, and orchids are all present in the Sphagnum mat zone of the bog and are valued as ornamental plants. The damaged caused by this issue is twofold. The loss of the plants is the major issue, but there is also damage caused by the poachers walking across the bog or Sphagnum mat. Other forms of destruction are also occurring from trespassing by hikers, ATV riders, horseback riders, and people
86 harvesting blueberries. While the bog is held as a preserve closed to the public, problems
still exist due to trespassing.
The major threat faced by Flatiron Lake Bog, which is the focus of this portion of
the characterization study of Flatiron Lake Bog, is changes in surrounding land uses to
more anthropogenic cover types. Changes to Flatiron Lake Bog with changes in the surrounding land uses can be determined using aerial photographs showing the area
surrounding this landholding, which can then be compared to the water chemistry and
vegetation results found in the current study versus the study conducted at Flatiron Lake
Bog in 1984 by Andreas and Bryan (1990).
Determination of Changes in Land Use
Changes in the land uses surrounding the Flatiron Lake Bog landholding were
determined by analyzing aerial photographs of the area from 1982 and the present (2006)
using ArcGIS. Land uses were classified and separated out from one another for all properties surrounding the bog for both time periods, and any changes that were observed during this 24-year time period were then recorded. Changes found during this time period were noted as either a major, complete change in land use (as from forestland to agriculture) or a minor change in land use practices (as in change in row crop agriculture to permanent cover crop agriculture).
Once any changes in land use type were determined, the potential effects this change could cause to Flatiron lake Bog were determined and compared to any changes in vegetation and water chemistry. Changes from forestland to agriculture, mining, or residential are assumed to have negative impacts to the bog and wetland complex. These changes from natural land cover types to anthropogenic land cover types can have
87 significant affects in the hydrology of a bog ecosystem, the water chemistry within the
bog, and the vegetation communities present in the ecosystem.
Agriculture increases the amount of nutrients being applied to the land adjacent to
a bog ecosystem and increases the potential for runoff into the wetland. This change from natural vegetation cover to agricultural crops with applied fertilizers increases the nutrient concentrations within a bog which is naturally nutrient-poor. Agricultural areas
may also increase the total amount of runoff entering the bog wetland complex through
tile drainage and a decrease in vegetative cover that normally reduces runoff flow rates
and aids infiltration to the groundwater. Residential areas pose the same problem of
potentially increasing the nutrient concentrations with lawn fertilizers and roads (salts,
oil, etc.), and the potential for increasing amounts of runoff increases with the amount of
impervious surfaces.
Determination of Changes in Vegetation
The vegetation sampling to determine any changes from 1984 to the present
followed the methodology of Andreas and Bryan (1990). The location of the vegetation
transects for this portion of the study were placed as close as possible to the original
transects used in 1984 (based on a field visit by Barbara Andreas during early summer
2007), and extend to a distance 20 m. The methodology of Andreas and Bryan was
different for the length of the transects in that they were to run to either 20 m or to the
outer edge of the tamaracks, whichever was longer. All of the results presented by
Andreas and Bryan (1990), however, only showed results to 20 m, so this length was
used in the current study.
88 The exact methods for determining the classification of vegetation into the
vegetation layers was not clearly defined in the publication by Andreas and Bryan (1990).
Therefore, some discrepancies in these transects for the different layers (tree,
shrub/sapling, herbaceous, and ground) are probable between this study in 2008 and the
study by Andreas and Bryan (1990) in 1984. For example, it appears that swamp
loosestrife was recorded in the shrub layer and herbaceous layer in 1984, but in the
current study was only recorded and measured in the herbaceous layer as the height of
this species was less than 1.37 m.
Four vegetation transects were established, one in each cardinal direction from the
edge of the open water area of the bog outward. These transects were one meter wide for
all herbaceous vegetation (taken as all vegetation under 1.37 m tall) and two meters wide
for all shrub and sapling vegetation (taken as all vegetation greater than 1.37 m tall but
less than 10 cm in diameter at breast height (dbh)). All trees that had branches overhanging any part of the two meter transect for shrubs were also measured and
recorded. Trees were considered all vegetation greater than 1.37 m tall and greater than
10 cm dbh. In the herbaceous layer, the transect was divided into 1-m² sections, which
were then further subdivided into twenty-five 20 x 20 cm subquadrats for determination
of relative density. Percent cover and number of 20 x 20 cm subquadrats the species was
present in were recorded for each species in the herbaceous transects, and number of
stems, diameter class, and percent cover was recorded for all species in the shrub and
sapling transects. Tree species and diameter (dbh) were recorded for each tree with
branches overhanging the other vegetation transects. Species names are taken from the
USDA Plants Database (Appendix A).
89 The results of the transects for this study were then compared to the results of
Andreas and Bryan (1990) and differences were determined in vegetation species and structure. The importance values for each species were calculated using the average of each species’ relative frequency (based on the number of subquadrats each species was present in per square meter plot for herbaceous and number of stems for shrubs, saplings, and trees) and relative dominance (based on the percent cover for each species for herbaceous and the basal areas for shrubs, saplings and trees). A percent relative change analysis on these importance values of the vegetation species was then completed for each species found in both studies to determine the percent relative increase or decrease in these species from 1984 to the present. All species found during only one of the studies were noted separately.
Determination of Changes in Water Chemistry
Changes in water chemistry over the same 24-year period were determined by
collecting water chemistry samples at similar locations as the study by Andreas and
Bryan (1990). Wells were constructed following methods from the US Army Corp of
Engineers (2005) using four inch PVC pipe to enable access by a YSI 6600 sonde and
YSI 650 multiparameter display system for water chemistry parameters and for water
sample collection. Following construction, one well was installed through the driving
method (driving into the peat using a rubber mallet to reduce disturbance along the
exterior sides of the wells) into the Sphagnum (or bog) mat in the shrub vegetation zone
within each of the four transects used in the vegetation portion of the study (Table 3.1,
Figure 3.4). The grab sample technique (collecting water from the open water with no well) was also used to collect water chemistry data from the edge of the open water
90 portion of the bog itself. The locations of the wells were placed as close as possible to the well locations used by Andreas and Bryan (1990), which were estimated by Barbara
Andreas during a field visit in early summer 2007.
Each well and grab sample location was sampled a total of eight dates in 2008:
July 10 and 24, August 7 and 21, September 4 and 18, and October 4 and 18. Water samples of 250 ml were collected in polypropylene bottles from the surface water of the well or the surface of the open water if a grab sample and were stored on ice until they could be sampled in the lab. The methods used in this study are based on the methods that were used by Andreas and Bryan (1990) for their sample collection in 1984. The methods presented in their publication, however, are not detailed and complete, and some differences in sampling procedures may have occurred, such as depth at which water samples were collected in the well, type of bottles used in collection, and location of the grab samples for the open water sample collection.
Table 3.1: GPS coordinates, transect and plot IDs, and type of collection for water sample collection sites (for both field and lab measurements) located within Flatiron Lake Bog, Portage County, Ohio. Latitude Longitude Sample Name Plot ID Type (N) (W) Andreas Transect South ATSOUTH Well 41.0444 81.3667 Andreas Transect North ATNORTH Well 41.0450 81.3669 Andreas Transect East ATEAST Well 41.0448 81.3665 Andreas Transect West ATWEST Well 41.0448 81.3668 Openwater ATOPEN WATER Grab 41.0444 81.3666
91
Figure 3.4: Location of wells and grab samples for water chemistry and nutrient analyses (for both field and lab measurements) within the Flatiron Lake Bog wetland area, Portage County, Ohio.
The YSI 6600 sonde and YSI 650 multiparameter display system was used to determine pH, temperature, and conductivity in the field from each sample location on each date (40 samples total, unique sample IDs in Table 3.2). Water samples were also collected at the same time and sent to the STAR lab at the Ohio Agricultural Research and Developmental Center (OARDC) for analysis of Ca and Mg concentrations. These concentrations were determined by the STAR lab through mineral analysis by ICP
(Inductively Coupled Plasma emission spectroscopy) after filtering through 0.45um membrane without acidification.
92 Table 3.2: Sample IDs for water chemistry samples (both field and lab) taken from the wells located within around the open water for Flatiron Lake Bog, Portage County, Ohio. Sample Date Sample Date ID Sample Name Sampled ID Sample Name Sampled ATE1 Andreas Transect East 7/10/2008 ATS5 Andreas Transect South 9/4/2008 ATE2 Andreas Transect East 7/24/2008 ATS6 Andreas Transect South 9/18/2008 ATE3 Andreas Transect East 8/7/2008 ATS7 Andreas Transect South 10/4/2008 ATE4 Andreas Transect East 8/21/2008 ATS8 Andreas Transect South 10/18/2008 ATE5 Andreas Transect East 9/4/2008 ATW1 Andreas Transect West 7/10/2008 ATE6 Andreas Transect East 9/18/2008 ATW2 Andreas Transect West 7/24/2008 ATE7 Andreas Transect East 10/4/2008 ATW3 Andreas Transect West 8/7/2008 ATE8 Andreas Transect East 10/18/2008 ATW4 Andreas Transect West 8/21/2008 ATN1 Andreas Transect North 7/10/2008 ATW5 Andreas Transect West 9/4/2008 ATN2 Andreas Transect North 7/24/2008 ATW6 Andreas Transect West 9/18/2008 ATN3 Andreas Transect North 8/7/2008 ATW7 Andreas Transect West 10/4/2008 ATN4 Andreas Transect North 8/21/2008 ATW8 Andreas Transect West 10/18/2008 ATN5 Andreas Transect North 9/4/2008 OW1 Openwater 7/10/2008 ATN6 Andreas Transect North 9/18/2008 OW2 Openwater 7/24/2008 ATN7 Andreas Transect North 10/4/2008 OW3 Openwater 8/7/2008 ATN8 Andreas Transect North 10/18/2008 OW4 Openwater 8/21/2008 ATS1 Andreas Transect South 7/10/2008 OW5 Openwater 9/4/2008 ATS2 Andreas Transect South 7/24/2008 OW6 Openwater 9/18/2008 ATS3 Andreas Transect South 8/7/2008 OW7 Openwater 10/4/2008 ATS4 Andreas Transect South 8/21/2008 OW8 Openwater 10/18/2008
Precipitation amounts were triangulated for the location of Flatiron Lake Bog.
The precipitation amounts by day from three weather stations currently used by NOAA were used in the triangulation: Stow (station number 338062), Ravenna (station number
336949), and Louisville (station number 334728) (www.noaa.gov, accessed April 24,
2009). These three stations were chosen for their location and proximity to Flatiron
Lake, as they were the three closest locations that were running through the summer of
2008 when the water level measurements were recorded.
The water chemistry results from this study were compared to the results presented by Andreas and Bryan (1990) from their study in 1984. A relative change 93 comparison was conducted for pH, conductivity, temperature, Ca concentrations, and Mg
concentrations to determine any relative changes in these characteristics.
3.3 Results
Changes in Land Use
An aerial photo from 1982 (Figure 3.5) was used from the USGS and compared to
a more current (2006) aerial photo (Figure 3.6) also from USGS to determine land use changes. Between the two photos, no major differences in adjacent land uses were
determined, and only a few slight changes were noted. All areas surrounding the Flatiron
Lake Bog property are in the same land use now as they were in 1982, two years prior to the study by Andreas and Bryan. Based on this finding, no aerial photographs between the starting and ending dates were analyzed.
Figure 3.5: Aerial photograph of the Flatiron Lake Bog property and adjacent properties from 1982, Portage County, Ohio.
94
Figure 3.6: Aerial photograph of the Flatiron Lake Bog property and adjacent properties from 2006, Portage County, Ohio.
The adjacent area to the north of Flatiron Lake Bog is residential in land use. The property lines that are evident from fence rows and abrupt changes from woodlot to yard on the aerial photograph from 1982 are still the same on the aerial photograph from 2006.
All of the houses on the properties to the north of Flatiron Lake Bog are older than 24 years, with no new development over this study time period.
From personal communication with the Flatiron Lake Bog land manager Karen
Adair, one small section of the agricultural fields to the west of Flatiron Lake Bog were changed to a permanent cover crop to reduce runoff, but personal observations from 2007 and 2008 indicate that there may not be an actual reduction in runoff with this change.
Raspberries have been planted here, with no permanent cover between rows (such as grass or other herbaceous) but are cut back in the winter and the fields are still exposed to
95 high runoff potential during the winter and spring months. The other agricultural fields
on the western edge of the Flatiron Lake Bog landholding remain in row crop agriculture.
The crops that have been grown in these agricultural fields are not known, but most
farming in Ohio is done on a rotation, with two or three crops being grown every year or
every third year, and is most likely the practice being used for this property.
The mining area to the south of the Flatiron Lake Bog property has changed from an active mining area to an inactive area. During the years that this gravel and sand mine
was operated, the water table below Flatiron Lake Bog was punctured, resulting in the
drainage of part of the wetland complex. While this was reversed through the use of a
water level control devise, the area is still in the process of being restored. With the
closing of this mine, the threat of other effects on the water table were removed.
The property on the eastern boundary of the Flatiron Lake Bog landholding has
remained the same over the 24-year study period. This property is the most natural land
use bordering the Flatiron Lake Bog landholding. It is residential in that it has a house
and barn (personal observation summers of 2007 and 2008), but it is forested and appears
to be managed for more passive recreational opportunities such as hiking.
Changes in Vegetation
The relative change in terms of percentages was determined for all species that
were present in the transects in both the study by Andreas and Bryan (1990) completed in
1984, and the current study from the summer of 2008. Species were compared by
vegetation layer (tree, shrub, herbaceous, and ground) and these changes were based on
each species’ importance values.
96 The tree vegetation layer had a total of three species during the current study: red maple, tamarack and yellow birch. During the study by Andreas and Bryan in 1984, only tamarack and yellow birch were recorded. Over the 24 year period between the two studies, tamarack decreased in importance (71 percent in 1984 to 30 percent in 2008), and yellow birch increased in importance (29 percent in 1984 to 62 percent in 2008) (Figure
3.7). Red maple had an importance value of eight percent in the current study in the tree layer.
Figure 3.7: Percent relative change of importance values in tree layer vegetation species from 1984 to 2008. Species shown are only those that were present during both study periods.
In 2008, we observed 11 sapling and shrub species, seven of which were also present in the 1984 study by Andreas and Bryan. One species, swamp loosestrife (18 percent importance value), was recorded in this layer in 1984 but not in the current layer.
Hackberry (Celtis occidentalis L.), blackgum (Nyssa sylvatica Marsh.), glossy buckthorn,
97 and poison sumac (Toxicodendron vernix (L.) Kuntze) were the species present in 2008,
but not in 1984 (Table 3.3). All of these species, however, had importance values of less
than one. Of the species present in both studies, mountain holly (Ilex mucronatus (L.)
Powell, Savolainen, and Andrews) (two percent in 1984 to six percent in 2008), yellow
birch (three percent to five percent), huckleberry (13 percent to 18 percent), and highbush
blueberry (32 percent to 45 percent) all increased in importance between 1984 and 2008,
but tamarack (seven percent to six percent) and leatherleaf (Chamaedaphne calyculata
(L.) Moench) (25 percent to three percent) both declined in importance over the time
period (Figure 3.8). Red maple remained the same in importance value over the 24 year
period, at two percent.
Figure 3.8: Percent relative change of importance values in shrub layer vegetation species from 1984 to 2008. Species shown are only those that were present during both study periods.
98 Table 3.3: Species in the shrub vegetation layer found in either 1984 (Andreas and Byran 1990) or in 2008 with associated importance values. Importance Value (%) Importance Value (%) Species 1984 2008 Celtis occidentalis 0 <1 Nyssa sylvatica 0 <1 Rhamnus cathartica 0 <1 Toxicodendron vernix 0 <1 Decodon verticillatus 18 0
The herbaceous layer had the highest species richness in either study, 1984 and
2008, and this layer’s species richness increased over the 24-year period. Nineteen
species were recorded in the current study that were not recorded during the study in
1984. All of these (purple chokeberry (Photinia floribunda (Lindl.) K.R. Robertson &
Phipps), blackgum, cinnamon fern (Osmunda cinnemomea (L.)), jewelweed (Impatiens
capensis L.), mountain holly, leatherleaf, huckleberry, goldenthread (Coptis trifolia (L.)
Salisb.), yellow-poplar (Liriodendron tulipifera L.), partridgeberry (Mitchella repens L.),
Virginia creeper (Parthenocissus quinquefolia (L.) Planch), black cherry (Prunus serotina Ehrh.), glossy buckthorn, greenbriar (Smilax rotundifolia L.), skunk cabbage
(Symplocarpus foetidis (L.) Salisb. Ex Nutt.), poison ivy (Toxicodendron radicans (L.)
Kuntze), poison sumac, Indian cucumberroot (Medeola virginiana L.), and arrowwood
(Viburnum recognitum Fernald) were present in the current study with importance values of less than one percent. Silvery sedge (Carex canescens L.), Virginia chain fern
(Woodwardia virginica (L.) Sm.), and bugleweed (Lycopis virginica Michx.) were all present in 1984, but not in 2008 (Table 3.4). Bog yellow-eyed grass (Xyris difformis
Chapm.) and bog sedge (Carex atlantica L.H. Bailey) remained the same in importance across the 24 year period.
99 Two of the herbaceous species recorded in both the study in 1984 and the current
study increased in importance (Figure 3.9): red maple (two percent in 1984 to three percent in 2008) and three-seeded sedge (Carex trisperma Dewey) (seven percent to eight
percent). The remaining seven species all decreased in importance over the 24 year
period: marsh St. Johnswort (Hypericum virginicum (L.) Raf.) (two percent to one
percent), white beak-sedge (Rhynchospora alba (L.) Vahl) (two percent to one percent),
tamarack (five percent to less than one percent), pitcher-plant (eight percent to less than
one percent), lesser bladderwort (Utricularia minor L.) (10 percent to three percent),
round-leaved sundew (13 percent to two percent), and large cranberry (Vaccinium
macrocarpon Aiton) (27 percent to one percent).
Table 3.4: Species in the herbaceous vegetation layer found in 1984 (Andreas and Bryan 1990) but not in 2008 with associated importance values. Species Importance Value (%) 1984 Carex canescens 7 Woodwardia virginica 7 Lycopus virginicus <1
100
Figure 3.9: Percent relative change of importance values in herbaceous layer vegetation species from 1984 to 2008. Species shown are only those that were present during both study periods.
In the ground vegetation layer, no species were found in 2008 that were not recorded in 1984. Five species, however, were recorded in 1984 but not in 2008 (Table
3.5). Of the species recorded during both studies, Cladopodiella flutians (four percent in
1984 to 1.2 percent in 2008) and Sphagnum recurvum (69 percent to 66 percent) both decreased in importance value over the 24 year period, and Sphagnum fibriatum (less than one percent to 3.7 percent), Aulacomnium palustre (two percent to 7.6 percent), and
Leucobryum glaucum (two percent to 20.5 percent) all increased in importance (Figure
3.10). 101 Table 3.5: Species in the ground vegetation layer found in 1984 (Andreas and Bryan) but not in 2008 with associated importance values. Species Importance Value (%) 1984 Cephalozia connivens 2 Mylia anomala 2 Sphagnum magellanicum 16 Sphagnum papillsum 2 Tetraphis pellucida 2
Figure 3.10: Percent relative change of importance values in ground layer species from 1984 to 2008. Species shown are only those that were present during both study periods.
The horizontal structure of the shrub layer surrounding Flatiron Lake Bog was recoded by Andreas and Bryan for the major shrub species recorded in 1984 by graphing the percentage cover by major species along a transect (from the average percent cover for each species by plot across the four transects used) from the open water lake into the shrub cover for a distance of 20 m (Figure 3.11). The same type of figure was created for
102 the same shrub species recorded in the current study for the summer of 2008 to compare the distribution of these species along this transect (Figure 3.12).
In both studies, swamp loostrife and leatherleaf were found the closest to the edge of the open water lake. These species then gradually are replaced by others with increasing distance from the open water. The swamp loosestrife and leatherleaf grade into primarily tamarack, huckleberry, and blueberry. The tamarack are present throughout the remainder of the 20 m transect in both the 1984 study and the current study, but in 1984, the huckleberry graded into the blueberry, whereas in the current study, the blueberry and huckleberry are mixed throughout the remainder of the transect without a major gradient. Mountain holly is found near the end of the transect the furthest into the shrub cover for both studies..
Figure 3.11: Smoothed curves of percentage cover of major shrubs along a transect from open water through 20 m for sampling during the summer of 1984 in Flatiron Lake Bog, Portage County, Ohio. Figure taken from Andreas and Bryan (1990).
103
Figure 3.12: Smoothed curves of percentage cover of major shrubs along a transect from open water through 20 m for sampling during the summer of 2008 in Flatiron Lake Bog, Portage County, Ohio.
A similar figure was created to show the distribution of Sphagnum mosses along the same 20 m transect (from the average percent cover for each species by plot across the four transects used). In 1984, Andreas and Bryan found primarily Sphagnum recurvum, with smaller percentages of S. fimbriatum and S. magellanicum after 18 m from the open water (Figure 3.13). During the summer of 2008, Sphagnum recurvum was still the major moss species, although the percentage cover was higher than recorded during the summer of 1984 (Figure 3.14). S. magellanicum was not recorded, but may have been missed in the sampling as it was found near the end of the transect in 1984 in smaller percentage cover. S. fimbriatum was more dispersed along the 20 m transect in
2008 than in 1984.
104 Figure 3.13: Smoothed curves of percentage cover of Sphagnum species along a transect from open water through 20 m for sampling during the summer of 1984 in Flatiron Lake Bog, Portage County, Ohio. Figure taken from Andreas and Bryan (1990).
Figure 3.14: Smoothed curves of percentage cover of Sphagnum species along a transect from open water through 20 m for sampling during the summer of 2008 in Flatiron Lake Bog, Portage County, Ohio.
Changes in Water Chemistry
Relative changes were determined for the water chemistry characteristics measured. The low range of pH values recorded in 2008 was similar to those recorded in
1984 for both the bog mat and the open water. In 2008, however, high range values for pH were higher than those reported by Andreas and Bryan in 1984 for both the open water and the bog mat. Conductivity was higher in 2008 and exhibited a wider range of values than in 1984, and temperature was lower in both the bog mat and open water in
2008 than in 1984. Calcium concentrations were similar during both studies, but showed less variability in 2008 than in 1984 for both the bog mat and the open water.
105 Magnesium was lower in both locations in 2008 than 1984, and, like the Ca
concentrations, had less variability in the current study.
The pH values recorded in the Sphagnum mat were lower than those recorded in
the open water due to the nature of Sphagnum to perpetuate acidic conditions as has been
recorded in other studies (Adema et al. 2005, Gunnarsson et al. 2000). Temperature in
the current study was lower in the bog mat than in the open lake, is potentially the result of high shade over the sample wells versus the open-water lake which has no cover, although this was not seen in the 1984 study.
Table 3.6: Chemical and physical characteristics of the open lake and Sphagnum mat (averaged for all four water sample locations) at Flatiron Lake Bog, Portage County, Ohio, for May-September 1985, and June-October 2008. Values for pH expressed as a range for the sampling periods, and conductivity, temperature, Ca and Mg expressed as mean and one standard deviation. Study Year and Conductivity Temperature Ca Mg pH Location mS/cm³ ⁰C mg/l mg/l 1984 Open Lake 4.1-4.3 44.0 ± 2.7 18.2 ± 2.8 2.8 ± 0.8 1.2 ± 0.4 Sphagnum Mat 3.5-4.2 45.7 ± 14.9 18.8 ± 2.4 2.9 ± 0.5 1.3 ± 0.4 2008 Open Lake 4.2-6.9 64.0 ± 46.0 17.6 ± 3.6 2.04 ± 0.21 0.69 ± 0.18 Sphagnum Mat 3.7-6.7 63.8 ± 43.3 15.5 ± 2.3 2.78 ± 0.72 0.86 ± 0.21
Several major precipitation events occurred throughout the course of the summer which impact the values recorded for the water chemistry characteristics (Figure 3.15).
The values used in the relative change comparison were averages across both summers
(1984 and 2008), but within each summer, individual values vary with the weather, especially with precipitation events. The majority of the rain accumulated in the months of July and September.
106
Figure 3.15: Precipitation amounts for the summer of 2008 at Flatiron Lake Bog, Portage County, Ohio.
3.4 Discussion
Changes in Land Use
Initially, it was believed that if changes were determined in the vegetation and
water chemistry parameters, changes would have occurred in the surrounding land uses.
This was not found to have occurred in the Flatiron Lake Bog area. Changes were
determined in the vegetation species importance values and the following water
chemistry characteristics: pH, conductivity, temperature, and Mg concentration, but no
major changes in the surrounding land uses were found over the 24-year time period from
1982 through 2006 (aerial photo dates). Although there was a change from row crop
agriculture to permanent cover crop agriculture in one field adjacent to Flatiron Lake
Bog, runoff is still occurring and flowing into the wetland complex (personal observations summers of 2007 and 2008). The amount of nutrients being applied
107 currently versus when the field was in row crops is not known, so changes in the nutrient
loadings by the agricultural landowner is also not known.
The mining area to the south of Flatiron Lake Bog is at a lower elevation, and
therefore does not influence the water entering the wetland complex like the agricultural
land use. This change in land use practice from active to inactive mine land was
completed between the years of 2001 and 2003, and is believed to only eliminate the
threats to the water table level, and not influence the water chemistry characteristics.
Restoration actions, such as the planting of grass over disturbed areas and filling of the quarry pit with water, have been undertaken in this mine land area.
Changes in Vegetation
Changes in the tree vegetation layer were important over the 24-year time period from 1984 to 2008. The importance value for tamarack, the tree species of highest concern for TNC, declined by over 50 percent. This is not, however, due to decreased numbers or basal area, but rather to increased importance of the other two tree species recorded. Yellow birch increased by over 100 percent in the tree vegetation layer from
1984 to 2008. Red maple was not recorded as a tree species in the study conducted in
1984, but had an importance value of eight percent in the current study.
Tamarack is regenerating in this area, and was present in the tree vegetation layer as well as the sapling layer and the herbaceous layer as seedlings, but as diversity increases with the introduction of red maple and the decreasing importance value of tamarack as red maple and yellow birch increase, this species eventually could be negatively impacted. Tamarack is a tree species adapted to the unique conditions that are often present in bogs, and are a shade intolerant species (Duncan 1954). With the
108 invasion of red maple onto the Sphagnum mat as a tree species, TNC faces a management issue in maintaining the native biodiversity of the landholding. Red maple is a shade- tolerant species (Hutnick and Yawney 1961), and once established, can shade out the regeneration of shade-intolerant species’ (such as tamarack).
The shrub vegetation layer also showed changes over the period from 1984 to
2008, but several of these are not necessarily actual changes in species importance values. The methods used by Andreas and Bryan (1990) in determining guidelines for placing vegetation within the different layers in 1984 were not clearly presented in their publication, which made it difficult to ensure that the measurements taken were consistent between the two studies. For example, swamp loosestrife, recorded in 1984 but not in 2008, was not recorded in the current study as a shrub species because it was below breast height. The decline seen in leatherleaf may also be attributed to this discrepancy in sampling methods. The methods used by Andreas and Bryan (1990) in determining guidelines for placing vegetation within the different layers in 1984 were not clearly presented in their publication, which made it difficult to ensure that the measurements taken were consistent between the two studies. Highbush blueberry, therefore, may only have increased in importance as a result of the loss of these two species from the total sum of importance values, as it had the highest recorded value and would reflect the largest difference.
The distribution of shrub species did change slightly (Figures 3.10 and 3.11). The overall shape of the curves (density at increasing distance from the open water portion of the bog) for most of the species are similar, except for leatherleaf, which was more condensed towards the open water in 2008 than it was in 1984 and for huckleberry, which
109 was more evenly distributed across the length of the transect in 2008 than in 1984.
Percentage cover for each individual species was lower in most of the transect in 2008,
but overall percent cover totals were similar for both study periods. These results are consistant with the other indicator for the diversification of Flatiron Lake Bog which is the increased diversity in the tree vegetation layer. Increasing diversity in the plant species richness in a bog ecosystem is generally the result of increasing nutrient concentrations in the water, which is potentially an effect of the agricultural runoff in the northwest corner of the wetland complex.
In the shrub and herbaceous vegetation layers, this vegetational diversification is clearly evident. Twenty-three species between these two vegetation layers were recorded in 2008 but not in 1984. All had importance values of less than one, and are not currently present at high enough importance values to be considered common, but attention needs paid to this issue as more time progresses. Diversification of the vegetation community in the bog could indicate changes in water chemistry from a semi-ombrotrophic bog to a poor-fen or other wetland type. This potential change in ecosystem type could require
TNC to change the management goals for this landholding, from maintaining the current diversity of community types and species, to managing for a more minerotrophic peatland that is more sustainable with higher nutrient levels.
In addition to the increase in species diversity, the herbaceous species that were present during both study periods (1984 and 2008) all changed in order of importance.
The species that declined in importance are the species typically found in the nutrient- poor conditions of a bog ecosystem, also indicating that the water chemistry of the area may be changing. While some of the species only changed by one or two percent,
110 pitcher-plant, sundew, and cranberry all declined by at least seven percent, which may be significant when considering management of the area. Gottelli (2002) found that increased nutrient inputs into bog ecosystems in New England reduced the reproduction and growth of pitcher plants, one of the species that has declined in Flatiron Lake Bog.
The ground vegetation layer changes may also be attributed to detection difficulties. Finding and identifying moss species within several of the sample plots proved to be difficult at times, and most of the species found in 1984 but not in 2008 had importance values of two percent, and may have been overlooked during the current study. The horizontal distribution of the different Sphagnum species with increasing distance from the open water also changed over this period. In 1984, Andreas and Bryan found primarily Sphagnum recurvum, with smaller percentages of S. fimbriatum and S. magellanicum further than 18 m from the open water. During the summer of 2008,
Sphagnum recurvum was still the primary moss species recorded, and the percentage cover at most sampling points was higher than recorded during the summer of 1984. S. magellanicum was not recorded in 2008, but may have been missed in the sampling as it was found near the end of the transect in 1984 with low percent cover. S. fimbriatum in general was more dispersed along the 20 m transect in 2008 than in 1984.
Different species of Sphagnum mosses require different habitat conditions for optimal growth. Sphagnum recurvum requires a lower pH than S. fimbriatum, but S. magellanicum requires the lowest pH (less than 4.9) of all three species (Ontario Ministry of Natural Resources 2008, Robroek et al. 2007)). S. magellanicum, therefore, is potentially declining in Flatiron Lake Bog as the pH increases, reducing this species’ competative advatage against S. recurvum and S. fimbriatum. This also supports the
111 conclusion from this study that the Flatiron Lake Bog ecosystem is changing from a
semi-ombrotrophic bog to a more minerotrophic peatland. A more detailed survey of the
Sphagnum mat specifically searching for this species is needed to determine whether it
has been lost from the ecosystem or not recorded in the transects used for the current
study.
Changes in Water Chemistry
The water chemistry changes observed between 1984 and 2008 also indicate that
there may be a shift occuring from a semi-ombrotrophic bog to a more minerotrophic
peatland type ecosystem. The pH and conductivity were slightly higher in 2008 than in
1984, but the temperature was slightly lower. Calcium remained fairly constant over the
24-year period, and Mg declined over the same time period.
The temperature differences noted cannot be adequately compared between the
two studies (1984 and 2008) since the exact methodologies from the study by Andreas
and Bryan (1990) are not known. Temperatures can change significantly with varying depths in the well and open water, and change with the ambient air temperature and precipitation. No conclusive comparisons can be drawn from these values without more information than was available for this study since the conditions present during sampling in 1984 are not known. For example, water temperatures decreased following the major precipitation events during the summer of 2008, and increased between these events, and
the dates for sampling in 1984 are not known, so comparisons of temperatures are
inconclusive and weak.
The parent material of the soils surrounding the wetland complex are low in
carbonates (USDA Soil Conservation Service 1978). This would indicate that the
112 increases in pH would not be caused by movement of water through the soil profile or from the parent material through the surface runoff or groundwater flows from the adjacent uplands. It is believed, therefore, that this increase in pH is caused by the continued inflow of runoff from the uplands that is less acidic.
The soil survey (USDA Soil Conservation Service 1978) for Portage County shows the soils in the adjacent agricultural fields as a Chili complex, which have soil pHs ranging from 4.5 to 6.5. These soils, in order to support row crop agriculture which have optimal pH ranges from 6.5 to 7.0, would typically be limed, where calcium carbonates would be added to the soil surface. While this practice was not seen during the summers of 2007 and 2008 on the fields directly adjacent to Flatiron Lake Bog, other agricultural fields in the general area of the landholding had been limed during the spring seasons of
2007 and 2008, so it is possible that the landowners adjacent to Flatiron Lake Bog lime their fields as well, which would result in higher levels of runoff containing calcium carbonate into the bog. Calcium has a low availability at pHs from 4.5 to 6.5, however, and does not become readily available to plants until a ph of greater than 6.5 is reached.
Therefore, due to the low pHs present at Flatiron Lake Bog, the calcium entering the wetland complex is not readily available to the plants in the bog community.
The changes that were observed in the vegetation and water chemistry are attributed to continued nutrient inputs from the agricultural area on the western border of the Flatiron Lake Bog property. There are currently three areas of known water inflow from the property to the west of Flatiron Lake Bog (Figure 3.16), two of which drain the agricultural fields specifically, and one drains a smaller remnant of the bog that has been separated from the larger complex owned by TNC.
113 The first of the inflow areas (Inflow 1 on Figure 3.16) draining the agricultural
fields was observed over the study time period (May 2007 through April 2009) to have
algal growth, orange discoloration, and steady flow rates during periods of higher
precipitation (early spring, and during noted events in Figure 3.15). These features
indicate that the water flowing into the wetland complex have higher nutrients to support
the algae, but that it may also have lower dissolved oxygen due to its presence. The
orange discoloration to the water indicates that during some periods of inflow in this
stream there are high iron concentrations. No actual water chemistry characteristics were
measured from this outflow, however.
This inflow source could cause problems in the management of Flatiron Lake Bog
in that the runoff entering the bog/wetland complex is richer in nutrients than this current
ecosystem type can support. The water entering the wetland complex from this agricultural field enters into the buttonbush shrub swamp vegetation community (Figure
3.3), which is less adapted to the nutrient-poor conditions of an ombrotrophic or semi- ombrotrophic bog. This buttonbush shrub swamp vegetation community supports a vegetation species composition that is not normally found in a semi-ombrotrophic bog such as Flatiron Lake Bog. While the buttonbush shrub swamp currently provides diversity both in terms of species richness and in community types, if this area increases in acreage over time, it will indicate that the water chemistry of the bog is becoming more enriched. This could eventually result in the loss of the bog ecosystem to a more diverse community composition, which is not the desired future outcome of TNC for this landholding. Bubier et al. (2007) working in the Mer Bleue Bog in Ottawa, Canada, found that with increasing nutrient additions to the bog ecosystem, plant composition
114 changed. They found, similar to the vegetation changes in the results of this study, that
with the addition of nutrients, the plant community became more diversified.
Figure 3.16: Aerial photograph showing the locations of the three know water inflow areas from the adjacent agricultural land use to the west of the Flatiron Lake Bog property, Portage County, Ohio. Inflow 1 is the intermittent stream draining the agricultural fields, inflow 2 is the drainage for the remnant of the bog in the middle of the adjacent agricultural fields, and inflow 3 drains the field with the permanent raspberry crop.
The second area of runoff adjacent to the agricultural fields (Inflow 3 on Figure
3.16) is located next to the raspberry crop, and has had silt fences previously installed to
help reduce the inflow of sediment into the wetland complex from the fields. These
fences, however, are no longer functional, since they have fallen apart and are no longer
standing. This is the agricultural area that evidenced minor change over the 24-year
period in terms of land use. In 1984, this area was in row crops similar to the fields to its 115 north and west. It was changed to raspberries after TNC raised concerns about the runoff
that was occurring from this agricultural field, but the effectiveness of this permanent
cover crop in reducing runoff is uncertain. When this area was observed during the field
work of 2007 and 2008, the fields had no permanent cover between the plants such as
grasses or other herbaceous plants, and were cut back in the late fall through the spring.
This allows water and sediment to continue to erode from this field towards the bog.
The final inflow point in this northwest corner of the Flatiron Lake Bog wetland complex (Inflow 2 on Figure 3.16) is a drainage pipe that comes from a small remnant of the bog on the Flatrion Lake Bog landholding that was cut off by the agricultural fields.
This inflow point does not come directly from and therefore directly drain the agricultural
fields, but the bog remnant is in the center of these fields, so runoff enters this small area
and is then drained into the wetland complex through a pipe running under the
agricultural field separating this remnant from the main portion of Flatiron Lake Bog.
While the water coming from the agricultural fields (the primary source of inflow
for the wetland complex, personal observation) was not sampled for water chemistry
characteristics, samples were collected from the wetland and lagg areas adjacent to this
inflow and pH, Ca, and Mg values were found to be higher than in the areas with no
agricultural runoff (Chapter 4). This water does not flow directly into the bog
community itself, but through the wetland complex surrounding it. The impacts this has on the bog may still be important, as the precise hydrological flow paths are not determined for Flatiron Lake Bog. The diversification of the vegetation community within the bog ecosystem lends credence to this hypothesis of changing pH in the water chemistry.
116 Flatiron Lake Bog may be experiencing accelerated succession due to the
increased nutrient inputs from the surrounding land uses, but would most likely
eventually reach a more diversified, minerotrophic fen type community over time
regardless. Kettle-hole bog succession typically changes along the gradient from ombrotrophic bog to semi-ombrotrophic bog to minerotrophic fen naturally (Adema et al.
2006). TNC, however, currently wishes to manage this property for the tamarack-
hardwood bog that is present as it is one of very few kettle-hole bogs remaining in Ohio.
Their goal is to maintain the natural diversity and species composition that is currently present. While the species richness in a bog ecosystem is not high, it is a unique community of plant species that are only found in the bog ecosystem due to the water chemistry characteristics. These species are found in very few other places in the state, and are species of high concern for TNC.
The water chemistry in bogs varies along a gradient for ombrotrophic to semi- ombrotrophic to weakly minerotrophic (Andreas and Bryan 1990). Ombrotrophic bogs are the most acidic peatland type, with very low nutrients (Ca 0.6-2.1 mg/l and Mg 0-0.2
mg/l), low pH (3.2-3.8), and low conductivity (12-27 mS/cm). Semi-ombrotrophic bogs have higher nutrients (Ca 1.5-3.5 mg/l and Mg 0.2-1.0 mg/l), slightly higher pH (3.7-4.2),
and higher conductivity (20-50 mS/cm). Weakly minerotrophic peatlands are the
boundary between bogs and fens, and are the most nutrient rich bog type (Ca 3.5-12 mg/l
and Mg 1.0-1.5 mg/l), with the highest pH (4-6) and conductivity (25-75 mS/cm)
(Andreas and Bryan 1990). Flatiron Lake Bog currently appears to be on the boundary
between a semi-ombrotrophic bog and a weakly minerotrophic peatland, whereas in
1984, this area was completely within the parameters of a semi-ombrotrophic bog. This
117 finding further supports the findings from the vegetation that Flatiron Lake Bog is becoming more diversified and is shifting towards a new ecosystem type.
These combined changes in vegetation and water chemistry parameters indicate that the tamarack-hardwood bog present at Flatiron Lake Bog may be slowly shifting to a more nutrient-rich peatland type. Although there have been no major changes and only a couple of minor changes in surrounding land uses that were evident through the comparison of aerial photographs and personal observations, continued runoff from agricultural fields directly into the wetland complex may be increasing the nutrients in this wetland complex. The amounts of nutrients added to the adjacent agricultural fields and the total runoff amounts were not determined in 1984, and personal observations on these were noted in 2008, but due to the lack of major change in land use, are not believed to have changed over the 24-year time period. The increasing vegetation diversity within Flatiron lake Bog, however, does indicate that the water chemistry values are changing, and that they are changing in a manner that will not maintain this community type without significant management actions.
3.5 Management Implications
In order to try and slow or reverse the increase in nutrients and pH within Flatiron
Lake Bog, more efforts need to be taken to control or filter the runoff coming in from the adjacent agricultural fields. Silt fences had been installed along one section of the agricultural fields at some point in time to control erosion, but have deteriorated to the point that they are no longer effective. These could be replaced to reduce the amount of erosion from the field into the wetland.
118 What is likely to be the main nutrient and runoff source, however, is a small
intermittent stream coming from the agricultural fields into the northwestern end of the
buttonbush shrub swamp vegetation community. Silt fences may help reduce sediments
coming into the wetland, but in order to reduce the high amounts of nutrients that may be
entering the wetland at this point, the water flow may need to be diverted away from the
wetland complex entirely. This could be done if a ditch was installed directing the water elsewhere. More study would need done before any action was taken to determine any potential negative impacts to the bog from possible management activities, e.g., changes in hydrology.
This installation of a diversion ditch would be highly controversial due to the
subsequent issues that it could cause in the bog. As this stream is currently considered a
principle source of water inflow for the Flatiron Lake Bog wetland complex, diversion of
the water may reduce the water levels within the wetland complex and lead to an even
higher increase in the rate of woody encroachment into the bog. Studies would need to
be established to assess the amount of water that actually enters the wetland complex
from this inflow point, and if the proportion of the total water volume of the wetland
from this source is high, this management action should not be undertaken, even with the
resulting reduction in nutrients. If the amount of water entering at this point does not
maintain the wetland water level to a high degree, though, it would reduce the amount of
nutrients entering and potentially slow the rate of change to a more minerotrophic
peatland.
The use of conservation buffers is another management option for reducing the
inflow of runoff and nutrients. Vegetated buffers surrounding the bog wetland complex
119 would slow the rate of runoff, and therefore would increase the rate of infiltration prior to
reaching the wetland complex. Having vegetated buffers also allows for the uptake of
nutrients by the plant species, which would reduce the concentrations reaching the
wetland complex. This potential management option could be more acceptable to the
general public than the controversial issue of managed drainage ditches, but could be
more difficult to implement due to higher costs in working with adjacent landowners and the potential for no or limited cooperation with these landowners.
It should be noted that eventually the natural succession of a semi-ombrotrophic bog (the peatland type classified in 1984 for Flatiron Lake Bog) is to, over time, become less nutrient-poor as it becomes more of a minerotrophic peatland. This implies that
Flatiron Lake Bog may be following this successional path, and the management of the area may need to be modified to incorporate this trend and to work towards the management of a more sustainable ecosystem such as a weakly minerotrophic peatland.
3.6 Conclusions
Overall, it appears that Flatiron Lake Bog is changing. Vegetation composition and species importance values have shown differences over a 24-year period from 1984 to 2008. Water chemistry parameters, such as pH, have also changed over this time period. However, the land uses on property adjacent to Flatiron Lake Bog over this same time period have remained relatively the same. Therefore, while the initial idea for this study was that changes in land use may change the vegetation and water chemistry of a bog, these results were not found. Yet changes in the vegetation and water chemistry did occur, and must therefore be caused by factors other than changes in land use type.
Continued affects of agricultural runoff with high nutrient loadings are believed to be
120 responsible for these changes, as increased nutrient concentrations and increased pH
values would result in the diversification of plant species diversity seen in this study.
Further studies need to be completed in order to fully assess the importance of changing water chemistry, vegetation, and the relationships that exist between these two defining features of bog ecosystems. Studies on the potential positive impacts of conservation buffers surrounding these ecosystem types may aid in the design of preserve
layouts for future conservation efforts to minimize the effects of runoff from adjacent
land uses.
The results found in this change detection portion of this study at Flatiron Lake
Bog help lay out a framework for assessing impacts of surrounding land uses to other
bogs in the region. Flatiron Lake Bog is a closed-landholding, with no allowable public
admittance. This provides an ecosystem without direct anthropogenic disturbances such
as trampling of the bog mat or installation of boardwalks, as are present at Triangle Lake
Bog. This lack of active anthropogenic disturbance allows for the assessment of the more passive anthropogenic disturbance of changing the surrounding land uses and the affects
this can have on the water chemistry and vegetation communities, and can aid in
determining similar changes in the other remaining kettle-hole bogs in Ohio and other
southern extremes of the natural bog ecosystem range.
121
CHAPTER 4
RELATIONSHIPS ALONG UPLAND/WETLAND GRADIENTS AT FLATIRON LAKE BOG
4.1 Introduction
Throughout the world bogs are found primarily in the boreal and cool temperate
regions of the world (Moore 2002). Bogs are wetland types that accumulate organic
material (peat), have acidic water and substrate, and are exclusively or primarily
precipitation fed (Moore 2002, Butovsky et al. 2004, Nordbakken et al. 2003). Due to
the nature of the water source and isolation from groundwater, bogs are nutrient-poor
wetland types, and support a unique flora composition. Sphagnum mosses are often the
most defining plant species in these ecosystems and their characteristics help perpetuate
the acidic, nutrient-poor water chemistry (Rochefort and Vitt 1990). Due to these conditions bogs often support populations of rare plant species, whether at the local, regional, or global scale (Topic and Stancic 2006, Butovsky et al. 2004).
Historically, the anthropogenic view of bogs has been utilitarian in nature (Mitsch
and Gosselink 2007). On the global scale, bogs have been areas of high conversion to
agricultural uses due to the high amounts of organic material, which after drainage results
122 in productive farm land. Peat has been and still is used as a source of fuel in many areas, and Sphagnum mosses are harvested for horticultural purposes. Throughout the past century, however, focus in bog ecosystems has shifted somewhat to a more conservation- based mindset (Butovsky et al. 2004, Topic and Stancic 2006, Tiemeyer et al. 2006).
Throughout the nineteenth and early twentieth centuries, Ohio peatlands were seen primarily as a resource for peat and sphagnum and as productive agricultural land once drained (Dachnowski 1912). Alfred Dachnowski’s Geological Survey of Ohio publication entitled Peat Deposits of Ohio: Their origin, formation, and uses (1912) lists the different peatlands surveyed across the state including location, size, quality of peat as a fuel, and potential productivity of the land if used for agriculture. This publication clearly outlines the prevailing view of the importance of peatland utilization during this time period.
More recently, the focus has changed from how to best utilize and exploit peatlands, to more of an emphasis on how to conserve and protect these ecosystem types
(Tomassen et al. 2004). One example of the more recent changing paradigm with respect to bog ecosystems is in Ohio. It is estimated that only four percent of the state’s original peatlands remain and support the typical vegetation of the ecosystem type (Andreas and
Knoop 1992). There are currently only three relatively undisturbed kettle-hole bogs left in Ohio, all of these under some sort of protection (Andreas and Bryant 1990). Flatiron
Lake Bog, located in southwest Portage County, is owned and protected by The Nature
Conservancy (TNC) and is closed to all public admittance. Fern Lake Bog, in Geauga
County, is a Cleveland Museum of Natural History Natural Area with limited access to the public (Cleveland Museum of Natural History
123 http://www.cmnh.org/site/Conservation_NaturalAreas_Map_FernLakeBog.aspx. March
31, 2009). Triangle Lake Bog, in Portage County, is the third relatively undisturbed kettle-hole bog in Ohio and is owned by the Ohio Department of Natural Resources
Division of Natural Areas and Preserves. This bog is open to the public, but has boardwalks installed to limit human impacts (ODNR Division of Natural Areas and
Preserves http://www.dnr.state.oh.us/location/triangle/tabid/967/Default.aspx. March 31,
2009).
The effects of the uplands on the wetland complex of Flatiron Lake Bog are not currently known. Runoff and inflow of nutrients may be substantial in some areas of the landholding, such as in the western area that is bordered by agriculture. Differences in water chemistry characteristics may be impacting the vegetation and soils of various areas of the wetland complex as well (Chapter 3). The goal of this study is to assess the changes in vegetation, water chemistry parameters, and soil characteristics across the upland/wetland at Flatiron Lake Bog to determine where the ecological wetland boundary exists in this ecosystem. Transects running along this gradient to observe changes in vegetation, soils, and water chemistry will then be compared to similar gradient transects to determine differences in these gradients with the influence of different adjacent land cover types.
4.2 Methods
Study Area Description
Flatiron Lake Bog is located in the southwestern corner of Portage County, Ohio
(N 41˚ 2’; W 81˚ 22’) and is one of the three remaining relatively undisturbed kettle-hole bogs in Ohio. TNC currently owns this bog, its surrounding wetland complex, and an
124 area of uplands surrounding this complex (Figure 4.1). The entire landholding is 39.2
hectares. The area is not open to the public due to the sensitive nature of the Sphagnum
mat and the potential damage that can be caused by human disturbances.
Figure 4.1: Aerial photo and boundary of the Flatiron Lake landholding (map created by TNC August 18, 2004).
The bog is located within the Little Cuyahoga River watershed (Subwatershed number 04110002-030-050), which ultimately drains north into Lake Erie. This watershed drains 4773.7 ha, from below the Mogadore Reservoir (Portage County, Ohio) to the Springfield Lake outlet (Summit County, Ohio)
(http://www.oh.nrcs.usda.gov/technical/14-digit/14narr04110002.html, accessed April 2,
2009). Flatiron Lake Bog constitutes 0.7 percent of the Little Cuyahoga Watershed.
125 This bog is representative of the concentric zones of vegetation typical of this
type of kettle-hole bog in the open water lake successional stage. The open water area is
surrounded by a floating Sphagnum mat with swamp loosestrife (Decodon verticillatus
(L.) Elliot), sundew (Drosera rotundifolia L.) and pitcher-plants (Sarracenia purpurea
L.) interspersed on the higher hummocks of the area. Surrounding the mat is a layer of
shrubs (primarily swamp loosestrife, highbush blueberry (Vaccinium corymbosum L.), and huckleberry (Gaylussacia baccata (Wangenh.) K. Koch)) with a ground layer of
Sphagnum, sundew, sedges (Carex spp.), pitcher plants, and other herbaceous species.
Outside of the shrub zone is a ring of tamaracks (Larix laricina (Du Roi) K. Koch), yellow birch (Betula alleghaniensis Britton), and red maple (Acer rubrum L.). The tamarack and yellow birch trees are at the southernmost extreme of their natural distribution.
The other areas of the wetland complex are a combination of two vegetation community types (Figure 4.2). The majority of the area is a mixed shrub swamp, dominated by blueberry shrubs and red maple and yellow birch trees. The other community type is a buttonbush shrub swamp, dominated by buttonbush (Cephalanthus occidentalis L.) and black willow (Salix nigra Marsh.). This community type is located in the northern area where agricultural runoff is a direct influence on the water chemistry.
The uplands of Flatiron Lake Bog are characterized by a diversity of overstory
tree species and shrubs, which constitute several different community types (Figure 4.2).
These include a mixed mesophytic forest, a beech-oak-red maple forest, an oak-hickory
forest, and an aspen stand. The upland areas owned by TNC are entirely forested,
although the uplands adjacent to its boundaries are not. On the western boundary of
126 Flatiron Lake Bog, agriculture (row crops) is the principle land use. To the north of the boundary is residential land use, and to the east is a less dense residential area with more forest cover than in the other three cardinal directions. The adjacent property to the south of Flatiron Lake Bog was previously mined, and is currently a lake where the gravel and sand was removed.
The soil in the bog and surrounding wetland complex is Carlisle muck (euic, mesic, typic Medisaprists), which is a very poorly drained Histosol (USDA Soil
Conservation Service 1978). This soil series has moderately rapid permeability and high available water capacity. The soil series on the upland portions of the Flatiron Lake Bog landholding include Chili (fine-loamy, mixed, mesic, typic Hapludalf) silt loam, 2 to 6 percent slopes, Chili gravelly loam, 6 to 12 percent slopes that are moderately eroded,
Sebring silt loam (fine-silty, mixed, mesic, typic Ochraqualfs), Chili-Wooster (Wooster – fine-loamy, mixed, mesic, typic Fragiudalfs) complex, 6 to 12 percent, 12 to 18 percent, and 18 to 30 percent slopes, Chili-Oshtemo (Oshtemo – coarse-loamy, mixed, mesic, typic Hapludalfs) complex, 12 to 18 and 18 to 25 percent slopes, and gravel pits (Figure
2.2). The parent material of the area is glacial till deposits of the Kent Moraine, which consists of high amounts of gravel and was deposited by a succession of glaciers and glacial retreats, from approximately 40,000 years before present until 15,700 years before present (Andreas and Bryan 1990).
127
Figure 4.2: Vegetation communities of the Flatiron Lake Bog landholding, Portage County, Ohio.
128
Figure 4.3: Soils of the Flatiron Lake Bog landholding, Portage County, Ohio.
It is not known exactly how water moves through the Flatiron Lake Bog wetland complex, but the general water flow paths are hypothesized based on field observations.
Water primarily enters the wetland complex from the northwest corner where there are three known sources of inflow from the adjacent agricultural fields (Figure 4.4). The first source of inflow is an intermittent stream draining the agricultural fields adjacent and to the northwest of Flatiron Lake Bog. The second source of water inflow drains a small remnant of the bog that is west-northwest of the bog that has been cut off from the main part in Flatiron Lake Bog by the agricultural fields. Finally, the third source of inflow is runoff from a field with a permanent raspberry crop. Runoff also occurs from the remaining adjacent uplands, but is not thought to be in the higher amounts seen from personal observations in the northwestern corner of Flatiron Lake Bog.
129
Figure 4.4: Aerial photograph showing the locations of the three know water inflow areas from the adjacent agricultural land use to the west of the Flatiron Lake Bog property and hypothesized hydrological flow paths. Inflow 1 is the intermittent stream draining the agricultural fields, inflow 2 is the drainage for the remnant of the bog in the middle of the adjacent agricultural fields, and inflow 3 drains the field with the permanent raspberry crop.
Water from these three known sources flows in a generalized northwest to southeast direction (Figure 4.4). Water from the first inflow (inflow 1) flows directly into the buttonbush shrub swamp in a southeastern direction towards the tamarack-hardwood bog. Water from the other two sources flow into the lagg area and are believed to flow around the wetlands in this lagg area towards the bog outflow on the eastern edge of the wetland complex. All of the water that enters the bog flows out of the wetland complex in an intermittent stream that flows out of the property on the eastern edge of the boundary. 130 Wetland Delineation
Delineation of the wetland boundary was conducted to determine the edge of the wetland complex surrounding the open water bog. Delineation of this area was completed using the 1987 U.S. Army Corp of Engineers Wetland Delineation Manual during late June and early July 2008. All common vegetation species were recorded, and the percent of wetland obligates and facultative wetland species was determined based on the total number of common plant species found in each sample. Standing water and other hydrological indicators such as redoxymorphic features in the soil and water lines on vegetation were recorded, and soil profiles were characterized including horizons, texture, color, presence and abundance of coarse fragments, and presence, colors and abundance of redoxymorphic features.
Delineation plots were established approximately every 20 m around the wetland edge. Each plot consisted of three samples: the first in an area of the wetland edge with standing water or water at the surface, the second within the boundary area with no obvious surface hydrological indicators, and the third in the edge of the upland area with no hydrological indicators and a change in elevation. Samples within the plots were determined to be within the wetland if the requirements for all three wetland indicators
(hydrology, hydric soils, and hydrophytic vegetation) were met. If one or more indicators were not met, the sample was determined to be within the upland. Sample field sheets are included in Appendix B.
Water Chemistry and Hydrology
The water chemistry and water levels for 13 wells, the open water portion of
Flatiron Lake Bog, and the wetland complex outflow were determined to provide an
131 overview of the characteristics of the hydrology and water chemistry throughout the wetland complex (Table 4.1, Figure 4.5). Four wells were located in transects immediately surrounding the open water of Flatiron Lake Bog (Transect ID: AT) and one grab sample (OPENWATER) was taken from the open water area itself. One of the remaining wells was installed and a grab sample was located in the outflow area for the bog and wetland complex (Transect ID: UWOF).
The remaining eight wells were placed within four transects located within the upland-wetland gradient in four locations with differing adjacent land uses (Transect IDs:
UWT1, UWT2, UWT3, and UWT4). The locations for these transects were chosen for several reasons. Two transects were chosen for their surrounding forest land use type and the other two for their surrounding agricultural land use type. The two forested transects were located in one area of gradual slope and the second in an area of greater slope to encompass the variety present in Flatiron Lake Bog. The two transects located adjacent to the agricultural land use were chosen based on the proximity to the two known areas of inflow from the agricultural fields. The wells were then located in the center of the lagg for the lagg wells, and 10 m into the wetland shrub cover from the lagg well for the wetland well. Ten meters was chosen as it was a distance that enabled all of the wetland wells to be within the wetland shrub cover. A shorter distance would have placed at least one well on the edge of the lagg area, and a greater distance would have placed one well in a large hummock that was determined to be too high above the wetland water level.
132 Table 4.1: GPS coordinates, transect and plot IDs, and type of collection for all water sample collection sites located within Flatiron Lake Bog, Portage County, Ohio. Transect Latitude Longitude Sample Name ID Plot ID Type (N) (W) UWT1WET UWT1 WET Well 41.0436 81.3669 UWT2WET UWT2 WET Well 41.0419 81.3677 UWT3WET UWT3 WET Well 41.0450 81.3683 UWT4WET UWT4 WET Well 41.0469 81.3694 UWT1LAGG UWT1 LAGG Well 41.0601 81.3668 UWT2LAGG UWT2 LAGG Well 41.0417 81.3678 UWT3LAGG UWT3 LAGG Well 41.0449 81.3685 UWT4LAGG UWT4 LAGG Well 41.0469 81.3696 Andreas Transect South AT SOUTH Well 41.0444 81.3667 Andreas Transect North AT NORTH Well 41.0450 81.3669 Andreas Transect East AT EAST Well 41.0448 81.3665 Andreas Transect West AT WEST Well 41.0448 81.3668 Openwater AT OPEN WATER Grab 41.0444 81.3666 Bog outflow UWOF BOG OUTFLOW Well 41.0435 81.3656 Wetland outflow UWOF COVE Grab 41.0435 81.3642
Wells were constructed following methods from the US Army Corp of Engineers
(2005) using four inch PVC pipe to enable access by a YSI 6600 sonde and YSI 650
multiparameter display system for water chemistry parameters and for water sample
collection. Following construction, one well was installed through the driving method
(driving into the peat using a rubber mallet to reduce disturbance along the exterior sides
of the wells) into the peat. The grab sample technique (collecting water from the open
water with no well) was also used to collect water chemistry data from the open water portion of the bog and the cove outflow.
133
Figure 4.5: Location of wells and grab samples for water chemistry and nutrient analyses within the Flatiron Lake Bog wetland area, Portage County, Ohio. Abbreviated sites: ATN = Andreas Transect North, ATE = Andreas Transect East, ATS = Andreas Transect South, ATW = Andreas Transect West, OW = Open Water, and BOGOUT = Bog Outflow.
Samples were taken from these locations on eight dates: July 10 and 24, August 7 and 21, September 4 and 18, and October 4 and 18. Due to low water levels, sample
UWT4LAGG and the wetland outflow sample were only able to be sampled on six of these dates (July 10 and 24, August 7 and 21, September 18, and October 4) and the
134 sample for UWT4WET was only able to be sampled on four dates (July 10 and 24,
August 7, and September 18).
A YSI 6600 sonde and YSI 650 multiparameter display system was used to
determine pH, temperature, conductivity, and percent dissolved oxygen in the field from
each sample location on each date (112 samples total, unique sample IDs, Tables 4.2 and
4.3). Water samples of 250 ml were also collected on the same dates as the YSI readings
in polypropylene bottles from the surface water of the well or the surface of the open
water if a grab sample. These were stored on ice until they were delivered to the lab.
The water samples were sent to the STAR lab at the Ohio Agricultural Research and
Developmental Center (OARDC) for analysis of nutrient concentrations for the following nutrients: P, K, Ca, Mg, S, Al, B, Cu, Fe, Mn, Mo, Na, and Zn. These concentrations were determined by the STAR lab through mineral analysis by ICP (Inductively Coupled
Plasma emission spectroscopy) after filtering. Only the nutrient results for P, K, and Ca
were used, since they were the only nutrients considered pertinent to this study.
Water levels were also recorded within each well for each sample date. Levels
were recorded with a Kesson tape as depth from the top of the well in cm, and were then
converted to actual depths (meters above sea level) based on the elevation of the top of
each well. The elevations for the top of each well was determined using relative change
readings from a total station from one known elevation within the Flatiron Lake Bog
landholding, located in the uplands directly adjacent to the bog outflow. These water level values were then used to more specifically characterize the patterns of water flow
throughout the bog and wetland complex.
135 Table 4.2: Sample IDs for water chemistry samples and water levels (*) taken from upland-wetland gradient wells and outflow locations for Flatiron Lake Bog. Sample ID Sample Name Date Sampled Sample ID Sample Name Date Sampled 1L1 UWT1LAGG* 7/10/2008 3L5 UWT3LAGG* 9/4/2008 1L2 UWT1LAGG* 7/24/2008 3L6 UWT3LAGG* 9/18/2008 1L3 UWT1LAGG* 8/7/2008 3L7 UWT3LAGG* 10/4/2008 1L4 UWT1LAGG* 8/21/2008 3L8 UWT3LAGG* 10/18/2008 1L5 UWT1LAGG* 9/4/2008 3W1 UWT3WET* 7/10/2008 1L6 UWT1LAGG* 9/18/2008 3W2 UWT3WET* 7/24/2008 1L7 UWT1LAGG* 10/4/2008 3W3 UWT3WET* 8/7/2008 1L8 UWT1LAGG* 10/18/2008 3W4 UWT3WET* 8/21/2008 1W1 UWT1WET* 7/10/2008 3W5 UWT3WET* 9/4/2008 1W2 UWT1WET* 7/24/2008 3W6 UWT3WET* 9/18/2008 1W3 UWT1WET* 8/7/2008 3W7 UWT3WET* 10/4/2008 1W4 UWT1WET* 8/21/2008 3W8 UWT3WET* 10/18/2008 1W5 UWT1WET* 9/4/2008 4L1 UWT4LAGG* 7/10/2008 1W6 UWT1WET* 9/18/2008 4L2 UWT4LAGG* 7/24/2008 1W7 UWT1WET* 10/4/2008 4L3 UWT4LAGG* 8/7/2008 1W8 UWT1WET* 10/18/2008 4L4 UWT4LAGG* 8/21/2008 2L1 UWT2LAGG* 7/10/2008 4L6 UWT4LAGG* 9/18/2008 2L2 UWT2LAGG* 7/24/2008 4L7 UWT4LAGG* 10/4/2008 2L3 UWT2LAGG* 8/7/2008 4W1 UWT4WET* 7/10/2008 2L4 UWT2LAGG* 8/21/2008 4W2 UWT4WET* 7/24/2008 2L5 UWT2LAGG* 9/4/2008 4W3 UWT4WET* 8/7/2008 2L6 UWT2LAGG* 9/18/2008 4W6 UWT4WET* 9/18/2008 2L7 UWT2LAGG* 10/4/2008 BO1 Bog outflow* 7/10/2008 2L8 UWT2LAGG* 10/18/2008 BO2 Bog outflow* 7/24/2008 2W1 UWT2WET* 7/10/2008 BO3 Bog outflow* 8/7/2008 2W2 UWT2WET* 7/24/2008 BO4 Bog outflow* 8/21/2008 2W3 UWT2WET* 8/7/2008 BO5 Bog outflow* 9/4/2008 2W4 UWT2WET* 8/21/2008 BO6 Bog outflow* 9/18/2008 2W5 UWT2WET* 9/4/2008 BO7 Bog outflow* 10/4/2008 2W6 UWT2WET* 9/18/2008 BO8 Bog outflow* 10/18/2008 2W7 UWT2WET* 10/4/2008 WO1 Wetland outflow 7/10/2008 2W8 UWT2WET* 10/18/2008 WO2 Wetland outflow 7/24/2008 3L1 UWT3LAGG* 7/10/2008 WO3 Wetland outflow 8/7/2008 3L2 UWT3LAGG* 7/24/2008 WO4 Wetland outflow 8/21/2008 3L3 UWT3LAGG* 8/7/2008 WO6 Wetland outflow 9/18/2008 3L4 UWT3LAGG* 8/21/2008 WO7 Wetland outflow 10/4/2008
136 Table 4.3: Sample IDs for water chemistry samples and water levels (indicated by *) taken from the wells located within around the open water for Flatiron Lake Bog, Portage County, Ohio. Sample Date Sample Date ID Sample Name Sampled ID Sample Name Sampled ATE1 Andreas Transect East 7/10/2008 ATS5 Andreas Transect South 9/4/2008 ATE2 Andreas Transect East 7/24/2008 ATS6 Andreas Transect South 9/18/2008 ATE3 Andreas Transect East 8/7/2008 ATS7 Andreas Transect South 10/4/2008 ATE4 Andreas Transect East 8/21/2008 ATS8 Andreas Transect South 10/18/2008 ATE5 Andreas Transect East 9/4/2008 ATW1 Andreas Transect West 7/10/2008 ATE6 Andreas Transect East 9/18/2008 ATW2 Andreas Transect West 7/24/2008 ATE7 Andreas Transect East 10/4/2008 ATW3 Andreas Transect West 8/7/2008 ATE8 Andreas Transect East 10/18/2008 ATW4 Andreas Transect West 8/21/2008 ATN1 Andreas Transect North 7/10/2008 ATW5 Andreas Transect West 9/4/2008 ATN2 Andreas Transect North 7/24/2008 ATW6 Andreas Transect West 9/18/2008 ATN3 Andreas Transect North 8/7/2008 ATW7 Andreas Transect West 10/4/2008 ATN4 Andreas Transect North 8/21/2008 ATW8 Andreas Transect West 10/18/2008 ATN5 Andreas Transect North 9/4/2008 OW1 Openwater 7/10/2008 ATN6 Andreas Transect North 9/18/2008 OW2 Openwater 7/24/2008 ATN7 Andreas Transect North 10/4/2008 OW3 Openwater 8/7/2008 ATN8 Andreas Transect North 10/18/2008 OW4 Openwater 8/21/2008 ATS1 Andreas Transect South* 7/10/2008 OW5 Openwater 9/4/2008 ATS2 Andreas Transect South* 7/24/2008 OW6 Openwater 9/18/2008 ATS3 Andreas Transect South* 8/7/2008 OW7 Openwater 10/4/2008 ATS4 Andreas Transect South* 8/21/2008 OW8 Openwater 10/18/2008
In order to determine the movement of water through the bog with precipitation events, precipitation amounts were triangulated for the location of Flatiron Lake Bog.
The precipitation amounts by day from three weather stations currently used by NOAA were used in the triangulation: Stow (station number 338062), Ravenna (station number
336949), and Louisville (station number 334728) (www.noaa.gov, accessed April 24,
2009). These three stations were chosen for their location and proximity to Flatiron
Lake, as they were the three closest locations that were running through the summer of
2008 when the water level measurements were recorded.
137 Soils
Soils were sampled along the four upland/wetland gradient transects in the three
areas of the ecotone: upland, lagg and wetland (Figure 4.6). Soil profiles were analyzed
to a depth of at least 60 cm, and were completed using either a soil auger or a shovel,
depending on the soil type. All lagg and wetland soils were profiled using the soil auger,
and all upland soils were profiled using a shovel to dig a soil pit. Horizons were visually
differentiated, depths of each horizon were measured with a Kesson tape, texture was
determined by feel, color was determined using the Munsell soil color charts, presence of
coarse fragments/gravel were estimated using the sheets provided in the Munsell color
book, presence and colors of mottles were determined, presence and size of roots were
estimated, and presence of water or other hydrological indicators were recorded.
Samples from the A and B horizons were removed from each soil profile and sent to the STAR Lab at OARDC in Wooster, Ohio. Each A horizon was analyzed for pH, available P, total N, exchangeable K and Ca, and CEC. The B horizon samples were
analyzed for everything tested in the A horizons with the exception of total N.
138
Figure 4.6: Locations of soil profiles along the upland/wetland transects at Flatiron Lake Bog, Portage County, Ohio. U = upland soil profile, L = lagg soil profile, and W = wetland soil profile.
Vegetation
Vegetation sampling for the upland/wetland gradients consisted of a 40 m long transect, with differing widths for different vegetation class measurements. The herbaceous vegetation layer was measured within a one meter wide transect, the shrub and sapling vegetation layer was measured in a two meter wide transects, and the trees were measured in a 10 m wide transect. These vegetation transects were centered on the
139 well located in the lagg portion of each upland/wetland transect, and from there ran 20 m
into the wetland and 20 m into the upland to determine variations along the entire transect
(Figure 4.7). UWT4 was shortened to 33 m in length due to the proximity of the Flatiron
Lake Bog property line. Species names are taken from the USDA Plants Database
(Appendix A).
Figure 4.7: Locations of the vegetation transects along the upland/wetland gradients in Flatiron Lake Bog, Portage County, Ohio.
Each herbaceous vegetation transect was divided into one by one-half meter squared subplot samples, the shrub and sapling layer into four by one-half meter squared subplot samples, and the tree layer into ten by one-half meter squared subplot samples.
Each of these subplot samples was recorded as being located in the upland, lagg or 140 wetland to allow for statistical analysis of the three areas. The distinction between plots
located in the upland and the lagg was based on the wetland boundary determined in the
wetland delineation portion of this study, and the distinction between lagg and wetland
was visually estimated based on vegetation species and changes from muck to more
peaty-muck or peat.
The one-meter wide transect was used as the center of each of the upland/wetland
transects, and within this width, all herbaceous species and woody vegetation under 1.37
m was recorded. For each species, the percent cover was visually estimated for the 0.5
m² sample. The frequency for each species was determined by further subdividing the
0.5 m² sample into twenty-five 20 x 20 cm subquadrats. The number of these 20 x 20 cm
subquadrats each species was present in was recorded. Relative frequency, relative dominance, and importance values were calculated by 0.5 m² sample plot for each species
following the methods in the vegetation community delineation portion of this study
(Chapter 2).
Using the centerline of the one-meter wide transect, a two-meter transect wide
was established and used to record the species, number of stems, and stem size classes
(less than 2.5 cm, 2.5-4.9 cm, 5.0-7.4 cm, and 7.5-9.9 cm) for all woody vegetation
greater than 1.37 m tall and less than 10 cm dbh. Relative density, relative dominance
and importance values were then calculated for each species by sample following the
methods used in the community delineation portion of this study.
Finally, to complete the vegetation transect, the 10 m wide transect was used to
sample all woody vegetation greater than 1.37 m tall and 10 cm dbh. This transect, like
the two-meter wide transect was also centered along the centerline for the one-meter wide
141 transect. For each living tree in this transect, the species and dbh were recorded.
Relative density, relative dominance and importance values were calculated by species following the methods used in the community delineation section of this study (Chapter
2).
Statistical Analysis
The importance values for all vegetation species was used for all 0.5 m² samples within all four of the upland/wetland transects (316 total samples) were used to run a detrended correspondence analysis (DCA) in order to examine the relationships between vegetation and location across the transect (uplands, lagg, and wetlands). Each sample was categorized as being in one of three categories: upland, lagg, or wetland. The samples were categorized based on which category was assigned during the vegetation sampling.
This DCA analysis was then refined on the same 316 samples with more discrete classifications to assess differences between the two transects with forested land use
(UWT1 and UWT2) and the two samples with adjacent agricultural land use (UWT3 and
UWT4). The categories used in this analysis were: upland and agriculture, upland and forest, lagg and agriculture, lagg and forest, wetland and agriculture, and wetland and forest.
To determine gradient differences within each transect, DCA analyses were then run on the vegetation data for each of the four upland-wetland transects individually. The axis 1 scores for each sample (0.5 m² sample plot) were then plotted against the distance along the transect to determine significant changes in the scores. The resulting graphs for
142 each of these four transects were then compared to determine any differences with the
differing adjacent land uses: forest versus agriculture.
We calculated Jaccard’s index for vegetation from each sample for each of the
four transects separately to determine any changes along the gradient in the beta diversity
using the following formula:
Jaccard’s index = C/(A+B+C)
Where: A = number of species in sample A, B = number of species in sample B, and C = number of species in both samples A and B. Index values were calculated comparing the
first 0.5 m² sample (sample A in the above formula) with the second (sample B in the
above formula), the second (sample A) with the third (sample B), and so on through the
entire length of the transect. These scores were plotted against the distance of the sample
along the transect in the same manner as the DCA axis scores to visually determine
significant changes in the index values.
Finally, the wetland indicator value (WIV) for each 0.5 m² plot along each of the
four transects were calculated and plotted against distance along the transect. WIV
numbers were calculated using the wetland indicator status for each species (which were
assigned during the wetland delineation portion of this study). The WIV is a calculated
score based on an assigned value for each wetland indicator status (e.g., OBL = 1,
FACW+ = 2, FACW = 3, FACW- = 4, FAC+ = 5, FAC = 6, FAC- = 7, FACU+ = 8,
FACU = 9, FACU- = 10, UP = 11) for each species in the sample, which are then
weighted by species abundance (Kirkman et al. 1998).
143 4.3 Results
Wetland Delineation
The wetland complex surrounding the bog itself was delineated using the 1987
U.S. Army Corp of Engineers Wetland Delineation Manual. All of the sample sites delineated as within the wetland boundary were found to have at least 50 percent hydrophytic vegetation, hydric soils, and hydrology of either water at the surface or within 12 in (30.48 cm) of the surface, following the guidelines established by the U.S.
Army Corp of Engineers Wetland Delineation Manual. Several delineation sites within the wetland boundary also had redoxymorphic features (mottling) present in areas of lower water levels, indicating that water levels fluctuate and are higher during some seasons of the year than when sampled. Delineation for this study occurred during summer with full vegetation and high evapotranspiration rates, resulting in lower water levels than are present during other seasons of the year, and some species that are only present early in the growing season may have been missed, which may influence the percent hydrophytic vegetation present in the sample plots, and may slightly influence the delineation of the actual boundary.
In the sample units located in the transition zone between the wetland and the upland, 25 of the 78 sample locations were determined to be within the wetland boundary. These 25 samples had at least 50 percent hydrophytic vegetation, hydric soils, and water or water indicators within 30.48 cm of the soil surface. Of the other 53 samples, four did not meet the vegetation requirement of 50 percent or greater of hydrophytic plants, 53 did not meet the hydrology requirements of water or water indicators within 30.48 cm of the surface, and six did not have hydric soils. These
144 samples from the center of the delineation transects were primarily used in the actual
determination of the boundary (Figure 4.8). Those that met all three requirements, and where the upland edge samples did not meet all three, were taken as the boundary, and for those that did not meet the requirements, the sample unit on the interior (wetland edge) of the transect was used as the wetland boundary delineation point. The sample units in the upland portions of the wetland delineation were nearly all located outside of the wetland boundary. Only two of these samples met the three wetland requirements, and in these two cases, were used as the delineation point for the wetland boundary.
Two sample points for the wetland delineation were considered outliers when the wetland boundary was mapped using ArcGIS (Figure 4.8). One “outlier” is a point in the southwest corner that is actually a small extension of the wetland to the west in a narrow area.
Figure 4.8: Wetland boundary determined by delineation transects and the ACOE Wetland Delineation Manual in Flatiron Lake Bog, Portage County, Ohio. 145 Vegetation
A DCA was run using the importance values for all sample plots along all
transects (316 total samples) using classifications for whether the plot was in the upland,
the wetland, or the lagg. When the axis 1 and axis 2 scores were plotted against each
other, this analysis shows very little differentiation between the three ecotone
classifications (Figure 4.9), especially in the lagg and wetland plots. The majority of the
upland samples, however, were more distinctly separated out from the lagg and wetland.
Figure 4.9: DCA axis scores for all ½ m² sample plots along the four upland-wetland gradient transects.
146 When the same statistical analysis was run with the classifications more discretely
differentiated (location and adjacent land use), clearer separations between all three
locations are revealed (Figure 4.10). Sample plots along the three transects were grouped
in one of six classifications for the DCA analysis: upland agriculture, upland forest, lagg agriculture, lagg forest, wetland agriculture, or wetland forest. These classifications reflect the different locations along the ecotone, but also reflect whether the adjacent land use is primarily forestland or agriculture. When the axis 1 and axis 2 scores were plotted against each other with these classifications or groupings, each of the six classes is more distinct from the other, as opposed to the DCA analysis with only the location classifications (wetland, lagg, or upland).
To assess the ecotone (wetland to upland) gradient changes along the upland/wetland transect, a DCA analysis was run on the sample plots for each transect individually. The DCA axis 1 scores that were assigned to each 0.5 m² plot along these transects were then graphed with the elevation changes along each upland/wetland transect to look for corresponding changes in both the elevation and the DCA scores.
The first transect (UWT1) was located in an area where the adjacent land use was forest cover. The difference in ground elevation from the first sample (in the wetland) and the last sample (in the upland) was 1.90 m. The distinction between the lagg and upland location areas is apparent when graphed due to an increase in ground elevation along with a corresponding increase in DCA axis 1 scores (Figure 4.11).
147 F igure 4.10: DCA axis scores for all ½ m² sample plots along the four upland-wetland gradient transects.
148
Figure 4.11: DCA axis 1 scores and elevations for 0.5 m² plots along the UWT1 transect plotted with elevations along transect. Distance along tansect: 0 m is within the wetland, and 40 m is within the upland. Lagg area well for water sample collection is located at 20 m. W/L indicates visual boundary between wetland and lagg; L/U indicates the visual boundary between lagg and upland; and ACOE indicates the U.S. Army Corp of Engineers (1987) wetland delineation boundary.
The second transect was similar to the first in that it is in an area of adjacent forest landcover. The difference in ground elevation from the first wetland sample to the last upland sample was greater than the first transect, with a difference of 3.20 m. The comparison of DCA scores to the changes in ground elevation along the transect also show similar increases where the lagg changes to the upland, but also shows one change in DCA scores where there is a hummock, and corresponding temporary increase in ground elevation (Figure 4.12).
149
Figure 4.12: DCA axis 1 scores and elevations for 0.5 m² plots along the UWT2 transect. 0 m is within the wetland, and 40 m is within the upland. Lagg area well for water sample collection is located at 20 m. W/L indicates visual boundary between wetland and lagg; L/U indicates the visual boundary between lagg and upland; and ACOE indicates the U.S. Army Corp of Engineers (1987) wetland delineation boundary.
The third transect was located in an area with agriculture as the adjacent land use.
This transect showed the least change in ground elevation from the beginning of the transect to the end, with a difference of only 0.87 m, and this minimal increase in elevation is also reflected by the gradual increase in DCA scores for the transect (Figure
4.13). There is no clear indication of transfer from one ecotone type to the next.
150
Figure 4.13: DCA axis 1 scores and elevations for 0.5 m² plots along the UWT3 transect. 0 m is within the wetland, and 40 m is within the upland. Lagg area well for water sample collection is located at 20 m. W/L indicates visual boundary between wetland and lagg; L/U indicates the visual boundary between lagg and upland; and ACOE indicates the U.S. Army Corp of Engineers (1987) wetland delineation boundary.
The fourth transect was located at the inflow area for the agricultural fields adjacent to Flatiron Lake Bog on the western boundary. These scores decreased as the transect moved into the uplands (Figure 4.14), unlike the other three, which increased.
The difference in ground elevation from the first wetland plot to the last upland plot was
1.36 m, and there is a correlation with the change from wetland to lagg with a sharper decrease in DCA scores.
151
Figure 4.14: DCA axis 1 scores and elevations for 0.5 m² plots along the UWT4 transect. 0 m is within the wetland, and 33 m is within the upland. Lagg area well for water sample collection is located at 15 m. W/L indicates visual boundary between wetland and lagg; L/U indicates the visual boundary between lagg and upland; and ACOE indicates the U.S. Army Corp of Engineers (1987) wetland delineation boundary.
Jaccard’s index, also a measure of beta diversity, had varied results in determining the separations between the wetland, lagg, and upland locations of the ecotone. This index measures the turnover of species, so high values indicate high rates of species composition changes. The first transect (UWT1) showed weak correlations between the
Jaccard’s values and the separation of wetland to lagg or lagg to upland (Figure 4.15).
The second transect (UWT2) showed distinct separations, but these were due to the lack of vegetation in the lagg area (Figure 4.16). The third transect (UWT3) also had no clear separations, similar to UWT1 (Figure 4.17). The fourth transect (UWT4) had no clear distinction between the wetland and lagg, but a decrease in Jaccard’s index values between the lagg and wetland (Figure 4.18).
152
Figure 4.15: Jaccard’s Index values and elevations for 0.5 m² plots along the UWT1 transect. 0 m is within the wetland, and 40 m is within the upland. Lagg area well for water sample collection is located at 20 m. W/L indicates visual boundary between wetland and lagg; L/U indicates the visual boundary between lagg and upland; and ACOE indicates the U.S. Army Corp of Engineers (1987) wetland delineation boundary.
Figure 4.16: Jaccard’s Index values and elevations for 0.5 m² plots along the UWT2 transect. 0 m is within the wetland, and 40 m is within the upland. Lagg area well for water sample collection is located at 20 m. W/L indicates visual boundary between wetland and lagg; L/U indicates the visual boundary between lagg and upland; and ACOE indicates the U.S. Army Corp of Engineers (1987) wetland delineation boundary. 153
Figure 4.17: Jaccard’s Index values and elevations for 0.5 m² plots along the UWT3 transect. 0 m is within the wetland, and 40 m is within the upland. Lagg area well for water sample collection is located at 20 m. W/L indicates visual boundary between wetland and lagg; L/U indicates the visual boundary between lagg and upland; and ACOE indicates the U.S. Army Corp of Engineers (1987) wetland delineation boundary.
154
Figure 4.18: Jaccard’s Index values and elevations for 0.5 m² plots along the UWT4 transect. 0 m is within the wetland, and 33 m is within the upland. Lagg area well for water sample collection is located at 15 m. W/L indicates visual boundary between wetland and lagg; L/U indicates the visual boundary between lagg and upland; and ACOE indicates the U.S. Army Corp of Engineers (1987) wetland delineation boundary.
The wetland indicator value was the least reliable method for determining changes between upland, wetland, and lagg areas. The lower the wetland indicator value, the higher the proportion of wetland species. The first transect (UWT1) had no distinctions in wetland indicator values for upland to lagg or lagg to wetland (Figure
4.19). UWT2 has a slight distinction in the transition from wetland to lagg, and more of a
distinct transition from lagg to upland (Figure 4.20). The third transect (UWT3) had a
gradual increase in wetland indicator values from wetland to lagg (Figure 4.21). The
fourth transect (UWT4) had an increase in values from the wetland to the lagg, and a
higher increase from the lagg to the wetland (Figure 4.22).
155
Figure 4.19: Wetland Indicator Values for 0.5 m² plots and elevations along UWT1. 0 m is within the wetland and 40 m is within the upland. Lagg area well is located at 20 m. W/L indicates visual boundary between wetland and lagg; L/U indicates the visual boundary between lagg and upland; and ACOE indicates the U.S. Army Corp of Engineers (1987) wetland delineation boundary.
Figure 4.20: Wetland Indicator Values for 0.5 m² plots and elevations along UWT2. 0 m is within the wetland and 40 m is within the upland. Lagg area well is located at 20 m. W/L indicates visual boundary between wetland and lagg; L/U indicates the visual boundary between lagg and upland; and ACOE indicates the U.S. Army Corp of Engineers (1987) wetland delineation boundary.
156
Figure 4.21: Wetland Indicator Values for 0.5 m² plots and elevations along UWT3. 0 m is within the wetland and 40 m is within the upland. Lagg area well is located at 20 m. W/L indicates visual boundary between wetland and lagg; L/U indicates the visual boundary between lagg and upland; and ACOE indicates the U.S. Army Corp of Engineers (1987) wetland delineation boundary.
157
Figure 4.22: Wetland Indicator Values for 0.5 m² plots and elevations along UWT4. 0 m is within the wetland and 33 m is within the upland. Lagg area well is located at 15 m. W/L indicates visual boundary between wetland and lagg; L/U indicates the visual boundary between lagg and upland; and ACOE indicates the U.S. Army Corp of Engineers (1987) wetland delineation boundary.
Soils
The soils from the upland plots along the upland to wetland transects varied widely from transect to transect. The first transect (UWT1) had six horizons (Table 4.4), and the parent material (gravel from glacial till) was reached at a depth of 58 cm. This soil profile is located in the oak-hickory forest cover type, and no human disturbance to denote an Ap layer was observed. This profile had high amounts of roots (both coarse and fine) throughout the profile down to the C horizon. Ten percent small gravel was found in the A horizon, and 30 percent small gravel was found in the B2 horizon. This soil does not match the entire description for the Chili silt loam series that it is classified as in the USDA Soil Conservation Service’s Soil Survey (1978). The A horizon is a loam, matching the series description, but is shallower than described. The underlying 158 horizons are sandier than the soil series description, but do have the underlying parent material of glacial sand and gravel.
Table 4.4: Soil profile for UWT1 upland plot from Flatiron Lake Bog, Portage County, Ohio. Depth (cm) Horizon Texture Color (Munsell) 2-0 O leaf litter 0-2 O fibric 2-9 A sandy loam 10YR3/1 9-13 B1 sand 10YR7/1 13-56 B2 loamy sand 10YR6/4 56+ C gravel 10YR6/4
The second transect (UWT2) had five horizons and was located in the mixed
mesophytic forest cover type (Table 4.5). This transect also had a higher clay content
(based on the texture by feel) in the B horizon, and a higher percentage of gravel in the B
horizon (40 percent, both small and medium). Both the first and the second transects’
upland soil profiles were very dry with no evidence of redoxymorphic features. This soil
does match the description given for the Chili-Wooster complex in the USDA Soil
Survey (1978). The A horizon is a loam, and the underlying horizons are have high sand
and gravel content.
Table 4.5: Soil profile for UWT2 upland plot from Flatiron Lake Bog, Portage County, Ohio. Depth (cm) Horizon Texture Color (Munsell) 4-0 O leaf litter 0-2 O fibric 2-10 A sandy loam 10YR3/3 10-41 Bt clay loam 10YR4/3 41+ C loamy sand 10YR4/6
The third transect (UWT3) was also very dry with no evidence of redoxymorphic
features, and had four distinct horizons (Table 4.6). This profile had only 15 percent
159 small gravel in the B horizon, but had higher silt content due to erosion from the adjacent
agricultural practices (Chili silt loam series). The parent material of glacial till with larger rocks was reached at a depth of 48 cm. This soil profile as classified in the USDA
Soil Survey (1978) is a Chili-Wooster complex, but with higher slopes than the soil for
UWT2. The soil profile described in this study has more features of the Chili series than
the Wooster series, but does have a mix of soil textures as is described for the complex.
Table 4.6: Soil profile for UWT3 upland plot from Flatiron Lake Bog, Portage County, Ohio. Depth (cm) Horizon Texture Color (Munsell) 3-0 O leaf litter 0-23 A clay loam 10YR5/4 23-45 Bt silty clay 10YR4/3 45+ C sandy clay 10YR4/3
The fourth transect (UWT4) had completely different upland soils than the first
three, and is directly adjacent to the agricultural fields (Table 4.7). This profile was clay texture completely through the profile below the top leaf litter. This soil had a B horizon with redoxymorphic features (10 percent) that was extremely hard with little ability for water to penetrate, and appeared to be close to a fragipan designation. This profile did not match the soil series description for the Chili silt loam, as it is classified in the USDA
Soil Survey (1978).
Table 4.7: Soil profile for UWT4 upland plot from Flatiron Lake Bog, Portage County, Ohio. Depth (cm) Horizon Texture Color (Munsell) Redoxymorphic Features 2-0 O leaf litter 0-19 Ap clay 10YR5/3 19+ Bg clay 2.5Y6/3 10%, orange mottling
160 The lagg soils were more similar across the first two transects (UWT1 and
UWT2) than the upland soil profiles were. The third and fourth transects (UWT3 and
UWT4) remained different from the first two. The first transect had four horizons, the
first three of which were organic (Table 4.8). The last horizon was an A horizon, and
appeared to have high organic matter content with 20 percent small gravel. The second transect had three profiles, all of which were organic (Table 4.9). This profile was slightly more decomposed than the first, without the more fibric peat layer on the surface.
Both the first and second transects met the description in the USDA Soil Survey (1978)
for Carlisle muck, the series this area is classified as.
Table 4.8: Soil profile for UWT1 lagg plot from Flatiron Lake Bog, Portage County, Ohio. Depth (cm) Horizon Texture Color (Munsell) 6-0 O leaf litter 0-4 Oi peat 4-56 Oe mucky peat
56+ A sandy clay loam 10YR2/1
Table 4.9: Soil profile for UWT2 lagg plot from Flatiron Lake Bog, Portage County, Ohio.
Depth (cm) Horizon Texture Color (Munsell) 4-0 O leaf litter 0-4 Oe peaty muck 4+ Oa muck
The third and fourth transects had less organic characteristics than the first two.
The third transect had only the leaf litter on the surface, and was then mineral soil below
(Table 4.10). This transect had higher clay content (based on the texture by feel) than the
others, and redoxymorphic features throughout the profile. The final transect (UWT4)
161 had an organic soil horizon, but which was buried beneath sediment from runoff from the
adjacent agricultural fields (Table 4.11). Both the A and B horizons had redoxymorphic
features, and the deepest horizon profiled was a brittle B horizon that was extremely hard
and had little ability for water penetration, similar to that seen in the upland soil profile.
Neither of these two transects were representative of the description in the USDA Soil
Survey (1978) for Carlisle muck.
Table 4.10: Soil profile for UWT3 lagg plot from Flatiron Lake Bog, Portage County, Ohio. Depth (cm) Horizon Texture Color (Munsell) Redoxymorphic Features 1-0 O leaf litter 0-27 Ag clay loam 10YR5/2 60%, orange mottling 27+ Bg silty clay loam 10YR2/1 45%, orange mottling
Table 4.11: Soil profile for UWT4 lagg plot from Flatiron Lake Bog, Portage County, Ohio. Depth (cm) Horizon Texture Color (Munsell) Redoxymorphic Features 0 - 23 Ag clay 10YR4/2 60%, orange/black mottling 23 - 47 Btg clay loam 10YR2/1 35%, orange mottling 47+ B2 clay 10YR8/1
The wetland soil profiles were similar for the first three transects (UWT1, UWT2,
and UWT3), with the fourth transect again different. The first three transects were all organic soils (Tables 4.12, 4.13, 4.14), the first transect being more decomposed than the
other three, and the second being the least decomposed. All three of these soil profiles
met the description in the USDA Soil Survey for the Carlisle muck soil series. The third
transect was influenced by the agricultural land use adjacent to the transect in that it had a
mineral soil horizon over the organic soils. The fourth transect was also influenced by
runoff from the adjacent agricultural fields, and had no organic soil, only a high clay
162 content A and B horizons (based on the texture by feel method) with redoxymorphic
features in the A (Table 4.15).
Table 4.12: Soil profile for UWT1 wetland plot from Flatiron Lake Bog, Portage County, Ohio. Depth (cm) Horizon Texture Color (Munsell) 2-0 O leaf litter 0-6 Oi peat 6+ Oe mucky peat
Table 4.13: Soil profile for UWT2 wetland plot from Flatiron Lake Bog, Portage County, Ohio. Depth (cm) Horizon Texture Color (Munsell) 6-0 O leaf litter 0-12 1Oe peaty muck 12+ 2Oe mucky peat
Table 4.14: Soil profile for UWT3 wetland plot from Flatiron Lake Bog, Portage County, Ohio. Depth (cm) Horizon Texture Color (Munsell) Redoxymorphic Features 0 - 12 Ag clay loam 10YR5/2 40%, orange 12 - 29 Oe peaty muck 29+ Oa muck
Table 4.15: Soil profile for UWT4 wetland plot from Flatiron Lake Bog, Portage County, Ohio. Depth (cm) Horizon Texture Color (Munsell) Redoxymorphic Features 3-0 O leaf litter 0-24 Ag clay 10YR4/2 5%, orange 24+ Bt clay loam 10YR3/2
Samples of the A and B horizons for each upland soil profile were sent to the
STAR lab at OARDC to determine pH, available P, exchangeable K and Ca, and percent
base saturation. The A horizon was also tested for total N. The pH was acidic for all transects in both the A and B horizons (Table 4.16). The first two transects (forested adjacent land cover) were more acidic, with pH values of 3.44 and 4.72 (A and B
163 respectively for UWT1) and 4.11 and 4.60 (A and B respectively for UWT2). These two transects also had lower base saturations (Table 4.17) and concentrations of available nutrients (excluding P). The total nitrogen for these two transects was lower than the other two samples associated with adjacent agricultural land use.
Table 4.16: pH and available P, K, and Ca for the A and B horizons of the upland soil profiles in the upland/wetland transects at Flatiron Lake Bog, Portage County, Ohio. Sample ID pH P (μg/g) K (μg/g) Ca (μg/g) UWT1 A 3.44 7 90 65 UWT2 A 4.11 44 76 126 UWT3 A 5.63 45 128 810 UWT4 A 4.87 51 126 298 UWT1 B 4.72 25 23 41 UWT2 B 4.60 59 54 58 UWT3 B 5.78 57 200 1178 UWT4 B 4.85 11 72 210
Table 4.17: Base saturation (percentages; A and B horizons) and total N (A horizon only) for the upland soil profiles in the upland/wetland transects at Flatiron lake Bog, Portage County, Ohio. Sample Base Saturation Total ID % Ca % K %N UWT1 A 1.2 0.8 0.341 UWT2 A 2.9 0.9 0.396 UWT3 A 37.8 3.1 0.108 UWT4 A 8.7 1.9 0.251 UWT1 B 2.1 0.6 - UWT2 B 2.0 1.0 - UWT3 B 50.3 4.4 - UWT4 B 7.7 1.4 -
Water Chemistry
The water samples taken from the wells in the wetland area of the wetland/upland transects were all analyzed for nutrient and mineral concentrations. The first nutrient
164 concentration determined was P, and varied across the four transects (Figure 4.23).
UWT2 had the highest P concentrations, followed by UWT3, and similar concentrations
for UWT1 and UWT4. All concentrations were less than 0.7 μg/ml. The second nutrient
analyzed was K, which had higher concentrations in the third and fourth transects than
the first and second (Figure 4.24), possibly due to fertilizer runoff from the adjacent
agriculture. Concentrations of K were higher than those of P, ranging from 0.975 to
7.177 μg/ml. The Ca concentrations within the wetland area wells of the wetland/upland
transects were similar for UWT1, UWT2, and UWT3 except for the last sample date for
UWT2, which was higher than the other values (Figure 4.25). UWT4 was slightly higher
during all sampling dates with water in the well than the other three transects.
Figure 4.23: Phosphorus concentrations for all wells located in the wetland areas of the upland to wetland transects in Flatiron Lake Bog, Portage County, Ohio. 165
Figure 4.24: Potassium concentrations for all wells located in the wetland areas of the upland to wetland transects in Flatiron Lake Bog, Portage County, Ohio.
166
Figure 4.25: Calcium concentrations for all wells located in the wetland areas of the upland to wetland transects in Flatiron Lake Bog, Portage County, Ohio.
The temperature of the water samples for the wetland wells all follow a similar pattern. Temperatures were higher at the beginning of the sampling period, and slowly fell throughout the course of the summer and early fall (Figure 4.26). The temperatures for UWT4 were consistently higher for the wetland samples, but this well was not under canopy closure of the shrub vegetation layer as the others were. Conductivity was low for UWT1, UWT3, and UWT4 and was fairly consistent throughout the summer, but values for UWT2 were higher and varied widely throughout the summer (Figure 4.27).
pH values for the transects were lower for UWT1 than the others for the duration of the summer (Figure 4.28). UWT2 was similar to UWT1 for the first half of the summer, and then increased near the end of the season. UWT3 and UWT4 were similar throughout the summer, and remained relatively constant. The percent dissolved O 167 varied widely throughout the summer, and values were not distinct across the four transects (Figure 4.29).
Figure 4.26: Water sample temperatures for all wells located in the wetland areas of the upland to wetland transects in Flatiron Lake Bog, Portage County, Ohio.
168
Figure 4.27: Conductivity for all wells located in the wetland areas of the upland to wetland transects in Flatiron Lake Bog, Portage County, Ohio.
Figure 4.28: pH for all wells located in the wetland areas of the upland to wetland transects in Flatiron Lake Bog, Portage County, Ohio. 169
Figure 4.29: Dissolved Oxygen (%) for all wells located in the wetland areas of the upland to wetland transects in Flatiron Lake Bog, Portage County, Ohio
The water samples taken from the wells in the lagg area of the wetland/upland transects were also analyzed for nutrient and mineral concentrations. P was fairly consistent throughout the summer in the lagg wells, except for UWT2, which increased sharply during the last sampling period (Figure 4.30). The second nutrient analyzed was
K, which had higher concentrations in the second, third, and fourth transects than the first
(Figure 4.31). UWT 2 had a sharp increase during the middle of the summer (September
4) that was not seen in the other transect samples. The Ca concentrations within the lagg area wells for the wetland/upland transects were varied across transects (Figure 4.32).
UWT4 was slightly higher than UWT3. UWT1 and UWT2 were lower than the other two for the first part of the summer, but after August increased. 170
Figure 4.30: Phosphorus concentrations for all wells located in the lagg areas of the upland to wetland transects in Flatiron Lake Bog, Portage County, Ohio.
Figure 4.31: Potassium concentrations for all wells located in the lagg areas of the upland to wetland transects in Flatiron Lake Bog, Portage County, Ohio. 171
Figure 4.32: Calcium concentrations for all wells located in the lagg areas of the upland to wetland transects in Flatiron Lake Bog, Portage County, Ohio.
The temperature of the water samples for the lagg wells all were higher at the beginning of the summer, and slowly fell throughout the course of the summer as did the wetland samples (Figure 4.33). The temperatures for UWT4 were also consistently higher for the lagg samples, but not as significantly as in the wetland sample temperatures, as this well had more of a shrub canopy cover. Conductivity was low for
UWT1, UWT3, and UWT4 and was fairly consistent throughout the summer, but values for UWT2 were higher but with less variability than it had for the wetland samples
(Figure 4.34). pH values for the transects were lower for UWT1 than the others for the duration of the summer (Figure 4.35). UWT2, UWT3, and UWT4 were similar
172 throughout the summer, and remained relatively constant. The percent dissolved O varied widely throughout the summer, and values were not distinct across the four
transects (Figure 4.36).
Figure 4.33: Water temperatures for all wells located in the lagg areas of the upland to wetland transects in Flatiron Lake Bog, Portage County, Ohio.
173
Figure 4.34: Conductivity for all wells located in the lagg areas of the upland to wetland transects in Flatiron Lake Bog, Portage County, Ohio.
Figure 4.35: pH for all wells located in the lagg areas of the upland to wetland transects in Flatiron Lake Bog, Portage County, Ohio. 174
Figure 4.36: Dissolved Oxygen (%) for all wells located in the lagg areas of the upland to wetland transects in Flatiron Lake Bog, Portage County, Ohio.
Hydrology
Once the elevations of the wells used for the determination of water levels and water flow patterns were calculated (Table 4.18), the water levels for these ten water sample locations were plotted out by sample date to help determine the hydrology of
Flatiron Lake Bog. All of the locations show the same trends in water level fluctuations except for the well located next to the open water (ATSOUTH) (Figures 4.37 and 4.38).
This sample remained fairly constant over the course of the summer. The water levels did show increases following high precipitation events.
175 Table 4.18: Elevations of the ten wells used to determine water level changes and water flow patterns in Flatiron lake Bog, Portage County, Ohio. Well top elevation Distance from top of well Ground Well ID (m) to ground surface (m) elevation ATSOUTH 306.67 0.16 306.67 UWT1WET 305.21 0.21 305.16 UWT1LAGG 305.65 0.26 305.54 UWT2WET 305.37 0.34 304.87 UWT2LAGG 305.81 0.46 305.32 UWT3WET 306.98 0.29 306.85 UWT3LAGG 306.29 0.30 306.15 UWT4WET 306.55 0.35 306.36 UWT4LAGG 306.69 0.45 306.40
Figure 4.37: Water levels (m above sea level) and precipitation for lagg area well samples in Flatiron Lake bog, Portage County, Ohio.
176
Figure 4.38: Water level elevations and precipitation for wetland area well samples in Flatiron Lake bog, Portage County, Ohio.
4.4 Discussion
Ecotones are a key component of any wetland ecosystem. This area is the transition from an upland ecosystem into the wetland ecosystem, and controls many factors within a wetland. This is especially true in a kettle-hole bog ecosystem such as
Flatiron Lake Bog, where the ecotone is a unit that includes the wetland edge, the lagg, and the upland edge. The delineation from one of these areas into the next is not always precisely defined by simply viewing the ecotone, although different parameters such as
177 vegetation, physical and chemical characteristics of the water, and soil characteristics can
help define where these areas are separate and where they grade together.
The vegetation at Flatiron Lake Bog was used to determine the boundaries of the
upland, lagg, and wetland using three different statistical methods. The first DCA
analysis run was only based on the classification of upland, lagg, or wetland locations for
the sample plots. This analysis did not clearly separate out the different locations and is
most likely the result of the differences in the transects themselves. When the axis 1 and
2 DCA scores were plotted for the different locations with adjacent land use categories,
these locations were separated more distinctly than without the adjacent land uses. This
indicates that the adjacent land use may be a controlling factor controlling vegetation
community composition within these transects. This is important when considering this
method for use in other wetland areas. If the adjacent land use is continuous for all areas
being studies, unlike the adjacent land uses to Flatiron Lake Bog, more general
classifications for the groupings would work well.
When the samples were classified based on groupings that included both the
location and the adjacent land use type, the samples with agricultural land use adjacent to the transect had overall lower axis 1 DCA scores than those samples with forestland as the adjacent land use. These results indicate that the diversity along the length of the transect is fairly consistent, without distinct separations between the wetland, lagg, and upland. The changes in plant species diversity along an ecotone is one of the defining features of the gradient from upland to wetland. This lack of change in diversity is likely a result of the agricultural runoff, which is more nutrient-rich than the water present in
178 the forested transects. The increase in nutrients allows more plant species to survive than
the natural, nutrient-poor characteristics of a bog ecosystem.
In these transects with adjacent agricultural land use, the plant species recorded in this study were not species typically associated with a bog ecosystem, but a wetland ecosystem that is more minerotrophic. This causes concern for the management of
Flatiron Lake Bog in that as the runoff from the agricultural fields continues, this nutrient-rich water slowly changes the plant composition farther and farther into the
wetland. The area that is affected by the agricultural runoff is in the northern area of the
wetland, and as the water in this area increases in nutrients, there is the potential for this
more diversified plant community to expand towards the tamarack-hardwood bog which
is the main management focus for TNC.
The adjacent land use for the four upland/wetland gradient transects was more
distinct than even the location in the ecotone in this statistical analysis. The adjacent land
use was an important factor in the calculations of the axis 1 DCA scores, whereas the
location (and hence the amount of water) was more evident in the axis two scores, and
therefore were considered less importantas the secondary factor by the statistical analysis.
Generally, when considering the ecotone from the upland areas into a wetland, the hydrology is considered most important. The DCA analysis completed for this study, however, indicate that there are factors such as adjacent land use that may mask the
underlying, physical and biological characteristics such as hydrology that separate the wetland from lagg and lagg from upland.
When each transect was analyzed using the DCA method separately, without the influences of different adjacent land uses, the distinction between wetland, lagg, and
179 upland were more pronounced. DCA axis 1 scores were lowest for the lagg area for
transects UWT1, UWT2, and UWT3. The lagg area was expected to have the lowest
DCA scores, since this area has the lowest species richness and diversity of the three
locations. The wetland areas for these three transects were intermediate in axis 1 scores
between the lower lagg scores and the upland area scores, which were higher than those
for the other two areas. These results were also expected since the wetland area has more
vegetation that the lagg, but has a low species richness and diversity due to the nutrient-
poor, acidic conditions that are present.
The fourth transect showed opposite results from the first three, however. This area is heavily impacted by agricultural runoff in the form of both water (inflow stream
from the adjacent agricultural fields) and in soil erosion, which is believed to be the
reason for the reversed DCA axis 1 scores. The wetland area in this transect is a diverse
mix of species that are not as nutrient-poor adapted as the wetland species recorded in the
other three transects, which are supported by the runoff entering the wetland at this point.
The lagg area at this transect had more vegetation than the other three transects, but still
had very low species diversity and richness as arrowwood (Viburnum recognitum) was
the dominant species.
The second statistical method used to determine boundaries between ecotone
areas based on vegetation was the Jaccard’s Index, which measures the vegetation species
turnover. This index did not separate out the ecotone areas well. The only transect that
showed clear results using this method was UWT2, where there was a distinct separation
in wetland to lagg and lagg to upland. Index values do not differ in this transect between
the wetland and upland, however. The distinction of the lagg area in this transect is due
180 to the almost complete lack of vegetation in this lagg area. This method for differentiating the wetland, lagg, and upland may be better suited to a slightly modified methodology, such as a larger sample size. Larger differences in plant species diversity would be found with this method if larger samples are used. It is possible that more distinct results for this statistical method would have been found in this study if a one
meter squared sample versus a one-half meter squared sample had been used.
Finally, a wetland indicator value (WIV) was used to try and determine the
boundaries of the ecotone components in Flatiron Lake Bog. This method again did not produce results as clear as those resulting from the DCA axis 1 scores, but did show distinctions in transects UWT2 and UWT4. UWT2 had lower WIV scores in the lagg
than the wetland and lower scores in the wetland than in the upland. This result, like that of the result from Jaccard’s index, is in part due to the lack of vegetation within the lagg portion of the ecotone. The score for the WIV method is the lower with more wetland- dependent plant species; therefore, a lower score would be expected in the wetland and lagg than in the upland.
UWT4 had lower results in the wetland than the lagg and lower results in the lagg than the upland. These results are what would be expected in an upland/wetland ecotone, as the wetland area should have the highest amount of wetland-dependent plants, which
would become less common and less dominant closer to the uplands.
However, these expected results of lower scores in the wetland and lagg than the
uplands were not found in the other three transects. These three transects showed high
variability in WIV scores across the entire length of the transect and is the result of the
sub-sample size used in the transects, similar to the problem noted with using Jaccard’s
181 index for this study. The WIV scores are affected by the number of species present, as
well as the wetland indicator statuses of the species, as it is weighted by the species’
abundance. The typical vegetation patterns within a peatland such as Flatiron Lake Bog
vary with hummocks and pools. More vegetation is found on the hummocks, which are
raised areas above the water table, than is found in the pools, which are constantly filled with water (Couwenberg 2005). The hummock areas within the transect in the wetland area would be expected to have higher WIV scores than the pools, but this difference would only be captured at the small sample size that was used in this study whereas it would not be seen at a larger sample size.
The soils for the upland/wetland transects were profiled in three areas along the transect: once in the upland, once in the lagg, and once in the wetland. The upland soils were more mineral in composition than the lagg and wetland, which were a varied combination of peat and muck. These results were expected, as the organic soils would decompose if not in the conditions of the wetland that slow decomposition, such as higher water levels. The majority of the soils profiled matched the descriptions found in the USDA Soil Survey (1978) for the area. Soil profiles from UWT4 and the soil profiles from the UWT3 lagg and wetland soils did not match the soil survey descriptions due to high disturbance in the form of erosion and runoff from the adjacent agricultural land use.
The soil profiles for UWT4 were completely different than those described in the soil survey, with no organic soils in the wetland area. The soils described in the wetland area for this transect were all mineral, although it is possible that at some depth there are buried organic soils.
182 The second transect did have a buried organic horizon under a mineral soil
horizon. The organic horizons profiled underneath the mineral horizon in this layer were
similar in texture and color to the organic soils found in the wetland areas of UWT1 and
UWT2, which leads to the conclusion that this area is receiving sediment from the
adjacent agricultural fields. The silt fences that had been installed in this area are no
longer standing, and the few pieces that are still intact hold pockets of sediment that has
been trapped in the fencing materials.
These differences between the soil survey descriptions and the descriptions from
this study indicate that the soils, like the vegetation, were affected by adjacent land use.
Although there are discrepencies between the soil survey and what exists on the ground
due to the scale of mapping by the USDA Soil Conservation Service, the buried organic horizon in UWT4 supports the idea that the agricultural land uses adjacent to Flatiron
Lake Bog are negatively impacting the wetland soils.
Transects with agricultural adjacent land use were more mineral than organic in the wetland and lagg samples due to the inflow of sediments from runoff coming from the upland agricultural fields. The soils from transects with this agricultural adjacent land use also had higher a higher pH in the upland soils than the forested transects, and higher concentrations of P, K, Ca, and N. The Ca concentration in UWT3 was much higher than the concentrations seen in all other transects (810 μg/l in the A horizon and 1178 μg/l in the B horizon). This increased concentration of Ca supports the conclusion that runoff is
still occurring at a high rate from the agricultural field with the permanent cover crop. If these soils are entering the wetland complex through erosion of the adjacent fields, the nutrients in the soil are also entering the wetland complex, supporting the conclusion that
183 the wetland is becoming more diversified with incoming nutrients from the adjacent
agricultural fields from the precious chapter in this study (Chapter 3).
These increased nutrient levels in the soil pose a threat in the spread of the
vegetation species present in UWT4 that resulted in the reverse DCA axis 1 scores than
the results from the other three transects. This potential spread of less nutrient-poor adapted species could displace the species that are present in and unique to the kettle-hole bog present at Flatiron Lake. These nutrient-poor species are the species that prompted
TNC to purchase this property, and are desired as a community that is naturally rare in
Ohio. The threats posed by agricultural runoff into the wetland complex surrounding the bog include the loss of these species. The hypothesized hydrological flows of Flatiron
Lake Bog show the water flowing from the inflow points at the adjacent agricultural land use southeast directly towards the tamarack-hardwood bog community.
The water chemistry, like the vegetation and soils, also varied between the wetland and lagg. Water chemistry was not determined for the uplands, as these areas were generally dry and did not have wells installed, so only the wetland and lagg areas were compared. In general, P, K, and Ca concentrations were higher in the lagg areas than in the wetland areas for all transects. This would be expected with the hypothesized hydrological flow patterns for Flatiron Lake Bog. Water from the inflow areas at the adjacent agricultural fields is believed to enter the wetland complex and then flow through the lagg to the wetland outflow. The nutrients from the agricultural runoff would therefore be more concentrated in the lagg area that it is flowing through than in the adjacent wetland.
184 Water temperatures and conductivity were similar between the wetland and lagg areas, and varied with major rainfall events throughout the summer and early fall.
Conductivity increased following large amounts of precipitation, and temperatures decreased. Values for pH were slightly higher for the lagg areas than for the wetland areas, which are expected with the higher percentage cover by Sphagnum mosses in the
wetland area than the lagg. Sphagnum mosses are present with high percentage cover in
the wetland areas, and their characteristics help perpetuate the acidic, nutrient-poor water
chemistry found in bog ecosystems (Rochefort and Vitt 1990).
Dissolved oxygen was higher in the lagg areas than the wetland areas for all transects. In the wetland area, however, it would be expected that the dissolved oxygen would be lower, as this is the area with the highest rate of peat accumulation. The low decomposition rates associated with the organic matter build up in this ecosystem would naturally be associated with low levels of oxygen. The lagg area also has flowing water, which although is slow for most of the year, would still result in an increase in dissolved oxygen.
Overall, the gradient from upland into wetland at Flatiron Lake Bog is differentiated into three main ecotone areas: wetland, lagg, and upland. The distinction from wetland to lagg is characterized by a decrease in vegetation species diversity, an
increase in nutrients, and less peat-textured organic soils. The transition from lagg to
upland is characterized by a sharp increase in vegetation species diversity, a sharp
increase in nutrient concentrations, and a water table that is present below the soil
surface.
185 The patterns of water flow within Flatiron Lake Bog appears to be fairly consistent across the wetland complex. All wells recorded the same patterns for water levels throughout the course of the summer, except for the well located immediately adjacent to the open-water portion of the bog, which remained constant. The wells located in UWT4 were dry several times throughout the summer. This finding supports the hypothesized flow pattern in Flatiron Lake Bog (Figure 4.4), because if the water
starts at the northwest inflow points and drains towards the southeast, the water would be
lower in this area during periods of little or no rainfall as the water flows through the
remainder of the wetland and towards the outlet.
The well located at ATSOUTH is adjacent to the open water portion of Flatiron
Lake Bog, and would therefore be expected to remain more stable during the course of
the summer than the areas around the edge of the wetland that would show more response
to short-term weather patterns. This well was located within the tamarack-hardwood bog, which is a raised-bog type ecosystem. The primary water source for this community is precipitation, so the well would not be influenced by sharp increases in runoff amounts as
the upland/wetland transect wells are.
4.5 Conclusions
The ecotone that exists between the upland areas and the wetland complex of
Flatiron Lake Bog are a very important component of the landscape. These ecotones
affect the vegetation, water chemistry, and soil parameters (such as pH, nutrient
concentrations, and texture) of all areas, including the wetland, the lagg, and the upland.
Adjacent land use has been shown to have high influence on some of these
186 characteristics, including nutrient concentrations, vegetation species diversity, and soil
profiles.
The most common approach to determining the boundary of a wetland is through
the use of the U.S. ACOE 1987 Wetland Delineation Manual. While this method will
delineate the outer boundary between the wetland and the upland, it does not give
detailed information on the ecotone that exists between these two different ecosystem
types. The ecotone between the upland and wetland is especially important in kettle-hole
bog ecosystems, where there is a lagg that acts as a water flow pathway through the
wetland complex. This area is also important in kettle-hole bog ecosystems in that this
ecotone is often the only buffer between the bog ecosystem and an anthropogenic land
use such as the agriculture that borders Flatiron Lake Bog. The wetland delineation
boundary, as determined by the U.S. Army Corp of Engineers wetland delineation
manual (1987), determined the boundary between the lagg and upland for three of the
four transects in this study, but has no means for determining boundaries between the wetland and lagg. The wetland delineation manual is also a more subjective method for determining the wetland boundary, whereas the statistical analyses are more objective.
Three statistical methods were used for determining the boundaries not only of the wetland as the U.S. Army Corp of Engineers Wetland Delineation Manual (1987) delineates, but also of the less discrete divisions within the gradient from wetland to upland were compared in this study. Of these three methods, the DCA analysis comparing DCA scores along the upland/wetland transect displayed the clearest separations between the wetland, lagg, and upland at Flatiron Lake Bog. The other two methods did not work very well with the sampling methods employed in this study.
187 Larger sample sizes within the transects would allow these methods to determine larger- scale differences, which is important with the small-scale topological differences that occur in the hummock-pool topography of peatlands. Any of these methods, with an appropriate study design and methodology, could be used with the U.S. ACOE wetland delineation method for a more detailed analysis of the wetland boundary and the ecotone that exists along this boundary from the upland into the wetland in all wetland types.
These methods may also be applicable in riparian areas to delineate the riparian corridor, if the limitations inhtese ecosystems are taken into account. Vegetation species composition may not be as clear in riparian systems as in wetlands due to factors such as terraces.
While the U.S. Army Corp of Engineers Wetland Delineation Manual is the accepted practice for wetland boundary delineation, it does not reflect the differences across the entire ecological wetland boundary. This method is for regulatory wetlands, not necessarily for ecological wetlands. The statistical methods presented in this study are more time consuming and detailed, but represent the entire gradient from the upland into the wetland. The U.S. Army Corp of Engineers manual is easier to implement, but in cases where the ecological boundary of a wetland is needed, may not be descriptive enough. The DCA axis 1 scores resulted in the best classification of different areas within the upland/wetland ecotone in Flatiron Lake Bog, and was more descriptive in determining the wetland boundary than the U.S. Army Corp of Engineers method.
The knowledge that was gained in this study helps to understand the underlying workings of Flatiron Lake Bog. This knowledge can be used in order to manage the area better than it is currently being managed. Knowing how each of the areas of the ecotone
188 affects the others, along with knowing how the differences in adjacent land use affects the ecotone as a whole can be used to determine the most important threats not only to
Flatiron Lake Bog, but also to other kettle-hole bogs in the region.
Further research needs completed in order to better understand the effects of adjacent land use, including land uses other than agriculture and forest, on kettle-hole bog ecosystems. The reduction in the effects of these land uses through the the use of different buffer widths of natural vegetation (such as forestland) also needs studied in order to better understand how to best manage these ecosystems. The methods and results from this study can be used as a basic framework on which to build these other necessary studies.
189
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194
APPENDIX A:
SCIENTIFIC AND COMMON NAMES OF PLANTS AT FLATIRON LAKE BOG
Nomenclature from USDA Plants Database
195 Species Scientific Name Common Name Code Acer rubrum L. Red maple ACRU Acer saccharum Marsh. Sugar maple ACSA Actaea racemosa L. Black cohosh ACRA Ailanthus altissima (Mill.) Swingle Tree-of-heaven AIAL Alliaria petiolata (M. Bieb) Cavara & Grande Garlic mustard ALPE Amelanchier spp. Serviceberry AMEL Andromeda polifolia L. Bog-rosemary ANPO Aralia nudicaulis L. Wild sarsaparilla ARNU Arisaema dracontium (L.) Schott Green-dragon ARDR Photinia floribunda (Lindl.) K.R. Robertson & Phipps Purple chokeberry ARPR Aulacomnium palustre AUPA Betula alleghaniensis Britton Yellow birch BEAL Calla palustris L. Wild calla CAPA Carex atlantica L.H. Bailey Bog sedge CAAT Carex canescens L. Silvery sedge CARCA Carex crinita Lam. Short-hair sedge CACR Carex trisperma Dewey Sedge CATR Carpinus caroliniana Walter American hornbeam CACA Carya cordiformis (Wangenh.) K. Koch) Bitternut hickory CACO Carya glabra (Mill.) Sweet Pignut hickory CAGL Carya ovata (Mill.) K. Koch Shagbark hickory CAOV Castanea dentata (Marsh.) Borkh. American chestnut CADE Celtis occidentalis L. Hackberry CEOC Cephalanthus occidentalis L. Buttonbush CEPH Chamaedaphne calyculata (L.) Moench. Leatherleaf CHCA Coptis trifolia (L.) Salisb. Goldthread COTR Cornus alternifolia L. f. Alternate-leaf dogwood COAL Cornus florida L. Flowering dogwood COFL Corylus americana Walter American hazel COAM Crataegus spp. Hawthorn CRAT Decodon verticillatus (L.) Elliot Swamp loosestrife DEVE Dennstaedtia punctilobula (Michx.) T. Moore Hay-scented fern DEPU Diphasiastrum digitatum Dill. ex. A. Braun Running-pine DIDI Drosera rotundifolia L. Round-leaved sundew DRRO Fagus grandifolia Ehrh. American beech FAGR Fragaria virginiana Duchesne Wild strawberry FRVI Fraxinus americana L. White ash FRAM Fraxinus pennsylvanica Marsh. Green ash FRPE Gaylussacia baccata (Wangenh.) K. Koch Huckleberry GABA Glyceria striata (Lam.) Hitchc. Fowl mannagrass GLST Hamamelis virginiana L. Witch-hazel HAVI Hieracium spp. Hawkweed HEIR Hypericum virginicum L. Marsh St. Johnswort HYVI Ilex verticillata (L.) A. Gray Winterberry ILVE Impatiens capensis Meerb. Spotted touch-me-not IMCA Juncus canadensis J. Gay ex LaHarpe Canada rush JUCA Larix laricina (Du Roi) K. Koch Tamarack LALA 196 Leersia oryzoides (L.) Sw. Rice cutgrass LEOR Leucubryum glaucum LEGL Ligustrum vulgare L. Privet LIVU Lindera benzoin (L.) Blume Spicebush LIBE Liriodendron tulipifera L. Yellow-poplar LITU Lonicera maackii (Rupr.) Herder Bush honeysuckle LOMA Magnolia acuminata (L.) L. Cucumber-tree MAAC Maianthemum canadense Desf. Canada mayflower MACA Malus spp. Crabapple MALA Medeola virginiana L. Indian cucumber-root MEVI Mitchella repens L. Partridge-berry MIRE Ilex mucronatus (L.) Powell, Savolainen, & Andrews Mountain holly NEMU Nyssa sylvatica Marsh. Blackgum NYSY Osmunda cinnamomea L. Cinnamon fern OSCI Parthenocissus quinquefolia (L.) Planch Virginia creeper PAQU Persicaria virginiana L. Jumpseed PEVI Podophyllum peltatum L. Mayapple POPE Polygonum arifolium L. Halberd-leaf tearthumb POAR Populus deltoides Bartram ex Marsh. Eastern cottonwood PODE Populus grandidentata Michx. Bigtooth aspen POGR Potentilla recta L. Sulfur cinquefoil PORE Prunus avium (L.) L. Sweet cherry PRAV Prunus serotina Ehrh. Black cherry PRSE Prunus virginiana L. Choke cherry PRVI Pteridium aquilinum (L.) Kuhn Bracken fern PTAQ Quercus alba L. White oak QUAL Quercus bicolor Willd. Swamp white oak QUBI Quercus palustris Münchh. Pin oak QUPA Quercus rubra L. Red oak QURU Quercus velutina Lam. Black oak QUVE Rhamnus cathartica Mill. Glossy buckthorn RHCA Rhynchospora alba (L.) Vahl. White beak-rush RHAL Ribes spp. Gooseberry RIBES Rosa multiflora Thunb. Multiflora rose ROMU Rubus alleghaniensis Porter Blackberry RUAL Salix nigra Marsh. Black willow SANI Sambucus canadensis L. American elderberry SACA Sarracenia purpurea L. Pitcher-plant SAPU Sassafras albidum (Nutt.) Nees Sassafras SAAL Smilacina racemosa (L.) Desf. False Solomon’s-seal SMRA Smilax rotundifolia L. Common Greenbrier SMRO Solanum dulcamara L. Nightshade SODU Solidago spp. Goldenrod SOLI Sphagnum fibriatum SPFI Sphagnum recurvum SPRE Symplocarpus foetidus (L.) Salisb. Ex Nutt. Skunk-cabbage SYFO Taraxacum officinale F.H. Wigg. Common dandelion TAOF Tilia americana L. American basswood TIAM Toxicodendron radicans (L.) Kuntze Poison ivy TORA 197 Toxicodendron vernix (L.) Kuntze Poison sumac TOVE Trifolium pretense L. Red clover TRPR Ulmus americana L. American elm ULAM Ulmus rubra Muhl. Slippery elm ULRU Utricularia minor L. Lesser bladderwort UTMI Vaccinium corymbosum L. Highbush blueberry VACO Vaccinium macrocarpon Aiton Large cranberry VAMA Viburnum acerifolium L. Maple-leaved viburnum VIAC Viburnum prunifolium L. Blackhaw VIPR Viburnum recognitum Fernald Arrowwood VIRE Vitis riparia Michx. Riverbank grape VIRI Woodwardia virginica (L.) Sm. Virginia chainfern WOVI
198
APPENDIX B:
REPRESENTATIVE SAMPLE FORMS FOR WETLAND DELINEATION AT
FLATIRON LAKE BOG
199 DATA FORM (Revised) ROUTINE WETLAND DETERMINATION (1987 Corps Wetland Delineation Manual)
Project Site: Flatiron Lake Bog Date: June 11, 2008 Applicant/Owner: The Nature Conservancy County: Portage Investigator(s): Stephanie Colwell and Sandi Aupperle State: Ohio
Do Normal Circumstances exist on the site? Yes No Community ID: Flatiron Is the site significantly disturbed (atypical situation)? Yes No Transect ID: WD001 Is Area a Potential Problem Area? Yes No Plot ID: A Explanation of atypical or problem area:
VEGETATION (For strata, indicate T = tree; S = shrub; H = herb; V = vine) Dominant Plant Species Stratum Dominant Plant Species Stratum 1 Winterberry S 8 2 Spotted touch-me-not H 9 3 Blackgum T 10 4 Halberd-leaf tearthumb H 11 5 12 6 13 7 14 Hydrophytic Vegetation Indicators: % of Dominants that are OBL, FACW or FAC: 100% Check all indicators that apply & explain below:
Visual observation of plant species growing in areas of prolonged x Wetland plant database x inundation/saturation Morphological adaptations x Other (explain) Technical Literature Hydrophytic Vegetation Present? Yes No Rationale for All vegetation hydrophytic and growing in standing water decision/Remarks:
HYDROLOGY
Is it the growing Yes No Water Marks Yes No Oxidized Root Yes No season? On: (live root) soil Based on Channels <12 in. temp Shrubs/trees Drainage other (explain) Drift Lines Yes No Yes No Patterns Depth of inundation: ¼ average inches FAC-Neutral Local Soil Yes No Yes No Test Survey Data Depth to free water in Inches Sediment Water-Stained Yes No Yes No pit: Deposits Leaves Depth to saturated soil: All inches Other (explain): saturated Standing water ¼ inch deep across area, deeper in smaller spots Check all that apply and explain below: Stream, Lake, or Gage Data Aerial Photographs Other
Hydrology Present? Yes No
Rationale for Standing water, muck/peat saturated decision/Remarks:
200 SOILS
Map Unit Name Carlisle Muck Drainage Class: Very poorly drained (Series): Field Observations Confirm Taxonomy: Histisol Yes No Mapped Type? Profile Description: Mottle Matrix color Mottle colors Depth abundance size Texture, concretions, Horizon (Munsell Moist) (Munsell Moist) (inches) contrast structure, etc. 0-5 O muck Sand, high organic matter 5+ A 10YR2/1 content
Hydric Soil Indicators: (check all that apply) High Organic Content in Surface Layer of Sandy Histisol Reducing Conditions Soils Gleyed or Low-Chroma (=1) Histic Epipedon Organic Streaking in Sandy Soils Matrix Matrix Chroma with < 2 with Sulfidic Odor Listed on National/Local Hydric Soils List mottles Aquatic Moisture Mg or Fe Concretions Other (explain in remarks) Regime Hydric Soils Yes No Rationale for Soils saturated and taxonomically a histisol decision/Remarks:
WETLAND DETERMINATION (Circle) Hydrophytic Vegetation Yes No Is this Sampling Point Within a Yes No Present? Wetland? Wetland Hydrology Present? Yes No Hydric Soils Present? Yes No Rationale/Remarks: Standing water present, area poorly drained with all hydrophytic vegetation and hydric soils NOTES:
201 DATA FORM (Revised) ROUTINE WETLAND DETERMINATION (1987 Corps Wetland Delineation Manual)
Project Site: Flatiron Lake Bog Date: June 11, 2008 Applicant/Owner: The Nature Conservancy County: Portage Investigator(s): Stephanie Colwell and Sandi Aupperle State: Ohio
Do Normal Circumstances exist on the site? Yes No Community ID: Flatiron Is the site significantly disturbed (atypical situation)? Yes No Transect ID: WD001 Is Area a Potential Problem Area? Yes No Plot ID: B Explanation of atypical or problem area:
VEGETATION (For strata, indicate T = tree; S = shrub; H = herb; V = vine) Dominant Plant Species Stratum Dominant Plant Species Stratum 1 Blackgum T 8 2 Cinnamon fern H 9 3 Spotted touch-me-not H 10 4 Wild strawberry H 11 5 Blueberry S 12 6 Red maple T 13 7 Yellow birch T 14 Hydrophytic Vegetation Indicators: % of Dominants that are OBL, FACW or FAC: 75% Check all indicators that apply & explain below:
Visual observation of plant species Physiological/reproductive adaptations growing in areas of prolonged x Wetland plant database x inundation/saturation Morphological adaptations x Other (explain) Technical Literature Hydrophytic Vegetation Present? Yes No Rationale for decision/Remarks: Greater than ½ wetland species, trees swelled at base
HYDROLOGY
Is it the growing Yes No Water Marks Yes No Oxidized Root Yes No season? On: (live root) Based on soil Trees Channels <12 in. temp other Drainage Drift Lines Yes No Yes No (explain) Patterns Depth of inundation: inches FAC-Neutral Yes No Local Soil Yes No Test Survey Data Depth to free water 15 Inches Sediment Water-Stained Yes No Yes No in pit: Deposits Leaves Depth to saturated 15 inches Other (explain): soil: Water in soil pit at 15 inches Check all that apply and explain below: Stream, Lake, or Gage Data Aerial Photographs Other
Hydrology Present? Yes No
Rationale for Water within 25 inches of the soil surface with water marks decision/Remarks:
202 SOILS
Map Unit Name (Series): Carlisle muck Drainage Class: Very poorly drained Field Observations Confirm Mapped Taxonomy: Histisol Yes No Type? Profile Description: Matrix color Mottle colors Mottle Texture, concretions,
Depth (inches) Horizon (Munsell Moist) (Munsell Moist) abundance size contrast structure, etc. 0-8 O Mucky peat 8-9 A 7.5YR3/1 Sand 9+ B 10YR4/2 Sand
Hydric Soil Indicators: (check all that apply) High Organic Content in Surface Layer Histosol Reducing Conditions of Sandy Soils Gleyed or Low-Chroma (=1) Histic Epipedon Organic Streaking in Sandy Soils Matrix Matrix Chroma with < 2 with Listed on National/Local Hydric Soils Sulfidic Odor mottles List Aquatic Moisture Regime Mg or Fe Concretions Other (explain in remarks) Hydric Soils Present? Ye No Rationale for Soils saturated with water closer to surface than 25 inches and high organic matter decision/Remarks: throughout profile
WETLAND DETERMINATION (Circle) Hydrophytic Vegetation Present? Yes No Is this Sampling Point Yes No Within a Wetland? Wetland Hydrology Present? Yes No Hydric Soils Present? Yes No Rationale/Remarks: Met all three requirements – water present close to surface with high % hydrophytic vegetation and soils still a histisol NOTES:
203 DATA FORM (Revised) ROUTINE WETLAND DETERMINATION (1987 Corps Wetland Delineation Manual)
Project Site: Flatiron Lake Bog Date: June 11, 2008 Applicant/Owner: The Nature Conservancy County: Portage Investigator(s): Stephanie Colwell and Sandi Aupperle State: Ohio
Do Normal Circumstances exist on the site? Yes No Community ID: Flatiron Is the site significantly disturbed (atypical situation)? Yes No Transect ID: WD001 Is Area a Potential Problem Area? Yes No Plot ID: C Explanation of atypical or problem area:
VEGETATION (For strata, indicate T = tree; S = shrub; H = herb; V = vine) Dominant Plant Species Stratum Dominant Plant Species Stratum 1 Blueberry S 8 Red maple T 2 Chokecherry S 9 3 White oak T 10 4 Cinnamon fern H 11 5 Blackgum T 12 6 Partridgeberry H 13 7 Witch-hazel S 14 Hydrophytic Vegetation Indicators: % of Dominants that are OBL, FACW or FAC: 33% Check all indicators that apply & explain below:
Visual observation of plant species growing in areas Physiological/reproductive adaptations of prolonged inundation/saturation Wetland plant database Morphological adaptations Personal knowledge of regional plant communities Technical Literature Other (explain) Hydrophytic Vegetation Present? Yes No Rationale for decision/Remarks: Less wetland species than other two, no standing water
HYDROLOGY Water Marks Oxidized Root Is it the growing season? Yes No Yes No Yes No On: (live root) Based on soil temp None Channels <12 in. other Drainage Drift Lines Yes No Yes No (explain) Patterns Depth of inundation: inches FAC- Yes No Local Soil Yes No Neutral Survey Data Depth to free water in pit: Dry Inches Sediment Water-Stained Yes No Yes No Deposits Leaves Depth to saturated soil: Dry inches Other (explain): Check all that apply and explain below: Stream, Lake, or Gage Data Aerial Photographs Other
Hydrology Present? Yes No
Rationale for No indicators of water near ground surface, all dry decision/Remarks:
204 SOILS
Map Unit Name (Series): Chili gravelly loam Drainage Class: Well drained Taxonomy: Field Observations Confirm Mapped Type? Yes No Profile Description:
Matrix color Mottle colors Mottle Depth Texture, concretions, Horizon (Munsell Moist) (Munsell Moist) abundance size contrast (inches) structure, etc. 0-2 O 2-5 A 7.5YR2.1/1 Sand with high organic matter 5+ B 7.5YR4/1 Sand
Hydric Soil Indicators: (check all that apply) High Organic Content in Surface Layer of Sandy Histosol Reducing Conditions Soils Gleyed or Low-Chroma (=1) Histic Epipedon Organic Streaking in Sandy Soils Matrix Matrix Chroma with < 2 with Sulfidic Odor Listed on National/Local Hydric Soils List mottles Aquatic Moisture Mg or Fe Concretions Other (explain in remarks) Regime Hydric Soils Yes No Rationale for Although no water in soil pit, soils evidence some features of being hydric decision/Remarks:
WETLAND DETERMINATION (Circle) Hydrophytic Vegetation Present? Yes No Is this Sampling Point Within a Yes No Wetland? Wetland Hydrology Present? Yes No Hydric Soils Present? Yes No Rationale/Remarks: Sample not wetland, but soils still have high organic matter
NOTES:
205 DATA FORM (Revised) ROUTINE WETLAND DETERMINATION (1987 Corps Wetland Delineation Manual)
Project Site: Flatiron Lake Bog Date: June 12, 2008 Applicant/Owner: The Nature Conservancy County: Portage Investigator(s): Stephanie Colwell and Sandi Aupperle State: Ohio
Do Normal Circumstances exist on the site? Yes No Community ID: Flatiron Is the site significantly disturbed (atypical situation)? Yes No Transect ID: WD030 Is Area a Potential Problem Area? Yes No Plot ID: A Explanation of atypical or problem area: High agriculture runoff in stream flowing into wetland
VEGETATION (For strata, indicate T = tree; S = shrub; H = herb; V = vine) Dominant Plant Species Stratum Dominant Plant Species Stratum 1 Arrowwood S 8 2 Spotted touch-me-not H 9 3 Buttonbush S 10 4 Sawgrass H 11 5 12 6 13 7 14 Hydrophytic Vegetation Indicators: % of Dominants that are OBL, FACW or FAC: 100% Check all indicators that apply & explain below:
Visual observation of plant species growing in areas Physiological/reproductive adaptations X of prolonged inundation/saturation Wetland plant database X Morphological adaptations Personal knowledge of regional plant communities Technical Literature Other (explain) Hydrophytic Vegetation Present? Yes No Rationale for decision/Remarks: All wetland species, water at the soil surface
HYDROLOGY Water Marks Oxidized Root Is it the growing season? Yes No Yes No Yes No On: (live root) Based on soil temp Shrubs Channels <12 in. other Drainage Drift Lines Yes No Yes No (explain) Patterns Depth of inundation: 0 inches FAC- Local Soil Yes No Yes No Neutral Survey Data Depth to free water in pit: 0 Inches Sediment Water-Stained Yes No Yes No Deposits Leaves Depth to saturated soil: 0 inches Other (explain): Check all that apply and explain below: Stream, Lake, or Gage Data Aerial Photographs Other
Hydrology Present? Yes No
Rationale for Water at the surface of the soils, stream inflow from ag fields next to transect decision/Remarks:
206 SOILS
Map Unit Name (Series): Carlisle Muck Drainage Class: Very poorly drained Taxonomy: Histisol Field Observations Confirm Mapped Type? Yes No Profile Description:
Matrix color Mottle colors Mottle Depth Texture, concretions, Horizon (Munsell Moist) (Munsell Moist) abundance size contrast (inches) structure, etc. 30+ O Muck
Hydric Soil Indicators: (check all that apply) High Organic Content in Surface Layer of Sandy Histosol Reducing Conditions Soils Gleyed or Low-Chroma (=1) Histic Epipedon Organic Streaking in Sandy Soils Matrix Matrix Chroma with < 2 with Sulfidic Odor Listed on National/Local Hydric Soils List mottles Aquatic Moisture Mg or Fe Concretions Other (explain in remarks) Regime Hydric Soils Yes No Rationale for decision/Remarks: Soils saturated to the surface, histisol
WETLAND DETERMINATION (Circle) Hydrophytic Vegetation Present? Yes No Is this Sampling Point Within a Yes No Wetland? Wetland Hydrology Present? Yes No Hydric Soils Present? Yes No Rationale/Remarks: Sample inundated, all hydrophytic vegetation, and soils obviously hydric
NOTES: Sediment deposits evident in wetland area from agriculture runoff – impacting soils and possible vegetation in this area
207 DATA FORM (Revised) ROUTINE WETLAND DETERMINATION (1987 Corps Wetland Delineation Manual)
Project Site: Flatiron Lake Bog Date: June 12, 2008 Applicant/Owner: The Nature Conservancy County: Portage Investigator(s): Stephanie Colwell and Sandi Aupperle State: Ohio
Do Normal Circumstances exist on the site? Yes No Community ID: Flatiron Is the site significantly disturbed (atypical situation)? Yes No Transect ID: WD030 Is Area a Potential Problem Area? Yes No Plot ID: B Explanation of atypical or problem area: High agriculture runoff in stream flowing into wetland
VEGETATION (For strata, indicate T = tree; S = shrub; H = herb; V = vine) Dominant Plant Species Stratum Dominant Plant Species Stratum 1 Red maple T 8 2 Blueberry S 9 3 Spotted touch-me-not H 10 4 Virginia chain fern H 11 5 Arrowwood S 12 6 13 7 14 Hydrophytic Vegetation Indicators: % of Dominants that are OBL, FACW or FAC: 100% Check all indicators that apply & explain below:
Visual observation of plant species growing in areas Physiological/reproductive adaptations of prolonged inundation/saturation Wetland plant database x Morphological adaptations Personal knowledge of regional plant communities Technical Literature Other (explain) Hydrophytic Vegetation Present? Yes No Rationale for decision/Remarks: All hydrophytic plants
HYDROLOGY Water Marks Oxidized Root Is it the growing season? Yes No Yes No Yes No On: (live root) Based on soil temp Shrubs Channels <12 in. other Drainage Drift Lines Yes No Yes No (explain) Patterns Depth of inundation: inches FAC- Yes No Local Soil Yes No Neutral Survey Data Depth to free water in pit: 15 Inches Sediment Water-Stained Yes No Yes No Deposits Leaves Depth to saturated soil: 14 inches Other (explain): Check all that apply and explain below: Stream, Lake, or Gage Data Aerial Photographs Other
Hydrology Present? Yes No
Rationale for Water in soil pit at 15 inches, staining on leaves and bases of shrubs decision/Remarks:
208
SOILS
Map Unit Name (Series): Carlisle Muck Drainage Class: Very poorly drained Taxonomy: Histisol Field Observations Confirm Mapped Type? Yes No Profile Description:
Matrix color Mottle colors Mottle Depth Texture, concretions, Horizon (Munsell Moist) (Munsell Moist) abundance size contrast (inches) structure, etc. 0-7 O Muck 7-10 A 10YR2/1 Sandy loam 10+ B 10YR3/2 Sandy clay loam
Hydric Soil Indicators: (check all that apply) High Organic Content in Surface Layer of Sandy Histosol Reducing Conditions Soils Gleyed or Low-Chroma (=1) Histic Epipedon Organic Streaking in Sandy Soils Matrix Matrix Chroma with < 2 with Sulfidic Odor Listed on National/Local Hydric Soils List mottles Aquatic Moisture Mg or Fe Concretions Other (explain in remarks) Regime Hydric Soils Yes No Rationale for decision/Remarks: Soils saturated within 15 inches of surface, very moist above that, high organic matter
WETLAND DETERMINATION (Circle) Hydrophytic Vegetation Present? Yes No Is this Sampling Point Within a Yes No Wetland? Wetland Hydrology Present? Yes No Hydric Soils Present? Yes No Rationale/Remarks: Meets all three criteria – no standing water, but water below surface within required limits NOTES: Area with runoff from adjacent agriculture in stream next to transect – affecting soils and possibly water quality
209 DATA FORM (Revised) ROUTINE WETLAND DETERMINATION (1987 Corps Wetland Delineation Manual)
Project Site: Flatiron Lake Bog Date: June 12, 2008 Applicant/Owner: The Nature Conservancy County: Portage Investigator(s): Stephanie Colwell and Sandi Aupperle State: Ohio
Do Normal Circumstances exist on the site? Yes No Community ID: Flatiron Is the site significantly disturbed (atypical situation)? Yes No Transect ID: WD030 Is Area a Potential Problem Area? Yes No Plot ID: C Explanation of atypical or problem area:
VEGETATION (For strata, indicate T = tree; S = shrub; H = herb; V = vine) Dominant Plant Species Stratum Dominant Plant Species Stratum 1 Cottonwood T 8 Wild strawberry H 2 Red maple T 9 3 White oak T 10 4 Pin oak T 11 5 Arrowwood S 12 6 Poison ivy H/V 13 7 Blueberry S 14 Hydrophytic Vegetation Indicators: % of Dominants that are OBL, FACW or FAC: 56% Check all indicators that apply & explain below:
Visual observation of plant species growing in areas Physiological/reproductive adaptations of prolonged inundation/saturation Wetland plant database Morphological adaptations Personal knowledge of regional plant communities Technical Literature Other (explain) Hydrophytic Vegetation Present? Yes No Rationale for decision/Remarks: Species present more than ½ wetland species, but obviously not growing where there is innundation
HYDROLOGY Water Marks Oxidized Root Is it the growing season? Yes No Yes No Yes No On: (live root) Based on soil temp None Channels <12 in. other Drainage Drift Lines Yes No Yes No (explain) Patterns Depth of inundation: Dry inches FAC- Yes No Local Soil Yes No Neutral Survey Data Depth to free water in pit: Dry Inches Sediment Water-Stained Yes No Yes No Deposits Leaves Depth to saturated soil: Dry inches Other (explain): Check all that apply and explain below: Stream, Lake, or Gage Data Aerial Photographs Other
Hydrology Present? Yes No
Rationale for Soils very dry, no indicators of water near soil surface or of any periods of innundation decision/Remarks:
210
SOILS
Chili-Wooster Map Unit Name (Series): Drainage Class: Well drained complex Taxonomy: Field Observations Confirm Mapped Type? Yes No Profile Description:
Matrix color Mottle colors Mottle Depth Texture, concretions, Horizon (Munsell Moist) (Munsell Moist) abundance size contrast (inches) structure, etc. 0-2 O 2-6 A 10YR4/2 Silt loam 6-11 B 2.5Y3/4 Clay loam 11+ E 10YR7/2 Clay
Hydric Soil Indicators: (check all that apply) High Organic Content in Surface Layer of Sandy Histosol Reducing Conditions Soils Gleyed or Low-Chroma (=1) Histic Epipedon Organic Streaking in Sandy Soils Matrix Matrix Chroma with < 2 with Sulfidic Odor Listed on National/Local Hydric Soils List mottles Aquatic Moisture Mg or Fe Concretions Other (explain in remarks) Regime Hydric Soils Yes No Rationale for decision/Remarks: Soils dry, no evidence of redoxymorphic features or water near surface
WETLAND DETERMINATION (Circle) Hydrophytic Vegetation Present? Yes No Is this Sampling Point Within a Yes No Wetland? Wetland Hydrology Present? Yes No Hydric Soils Present? Yes No Rationale/Remarks: Elevation higher than samples A and B, no hydrology or soil indicators met
NOTES:
211 DATA FORM (Revised) ROUTINE WETLAND DETERMINATION (1987 Corps Wetland Delineation Manual)
Project Site: Flatiron Lake Bog Date: June 12, 2008 Applicant/Owner: The Nature Conservancy County: Portage Investigator(s): Stephanie Colwell and Sandi Aupperle State: Ohio
Do Normal Circumstances exist on the site? Yes No Community ID: Flatiron Is the site significantly disturbed (atypical situation)? Yes No Transect ID: WD053 Is Area a Potential Problem Area? Yes No Plot ID: A Explanation of atypical or problem area:
VEGETATION (For strata, indicate T = tree; S = shrub; H = herb; V = vine) Dominant Plant Species Stratum Dominant Plant Species Stratum 1 Bog sedge H 8 2 Blueberry S 9 3 Spotted touch-me-not H 10 4 Yellow birch T 11 5 12 6 13 7 14 Hydrophytic Vegetation Indicators: % of Dominants that are OBL, FACW or FAC: 100% Check all indicators that apply & explain below:
Visual observation of plant species growing in areas Physiological/reproductive adaptations x of prolonged inundation/saturation Wetland plant database x Morphological adaptations x Personal knowledge of regional plant communities Technical Literature Other (explain) Hydrophytic Vegetation Present? Yes No Rationale for decision/Remarks: Plants growing in inundated areas, all wetland species, basal swelling of trees
HYDROLOGY Water Marks Oxidized Root Is it the growing season? Yes No Yes No Yes No On: (live root) Based on soil temp Tree/shrub Channels <12 in. other Drainage Drift Lines Yes No Yes No (explain) Patterns Depth of inundation: ½ to 1 inches FAC- Yes No Local Soil Yes No Neutral Survey Data Depth to free water in pit: Inches Sediment Water-Stained Yes No Yes No Deposits Leaves Depth to saturated soil: 0 inches Other (explain): Check all that apply and explain below: Stream, Lake, or Gage Data Aerial Photographs Other
Hydrology Present? Yes No
Rationale for Standing water, inundated soils decision/Remarks:
212
SOILS
Map Unit Name (Series): Carlisle muck Drainage Class: Very poorly drained Taxonomy: Histisol Field Observations Confirm Mapped Type? Yes No Profile Description:
Matrix color Mottle colors Mottle Depth Texture, concretions, Horizon (Munsell Moist) (Munsell Moist) abundance size contrast (inches) structure, etc. Total O Muck sample
Hydric Soil Indicators: (check all that apply) High Organic Content in Surface Layer of Sandy Histosol Reducing Conditions Soils Gleyed or Low-Chroma (=1) Histic Epipedon Organic Streaking in Sandy Soils Matrix Matrix Chroma with < 2 with Sulfidic Odor Listed on National/Local Hydric Soils List mottles Aquatic Moisture Mg or Fe Concretions Other (explain in remarks) Regime Hydric Soils Yes No Rationale for decision/Remarks: Histisol, innundation
WETLAND DETERMINATION (Circle) Hydrophytic Vegetation Present? Yes No Is this Sampling Point Within a Yes No Wetland? Wetland Hydrology Present? Yes No Hydric Soils Present? Yes No Rationale/Remarks: Sample completely inundated with water, plants growing in standing water
NOTES:
213 DATA FORM (Revised) ROUTINE WETLAND DETERMINATION (1987 Corps Wetland Delineation Manual)
Project Site: Flatiron Lake Bog Date: June 12, 2008 Applicant/Owner: The Nature Conservancy County: Portage Investigator(s): Stephanie Colwell and Sandi Aupperle State: Ohio
Do Normal Circumstances exist on the site? Yes No Community ID: Flatiron Is the site significantly disturbed (atypical situation)? Yes No Transect ID: WD053 Is Area a Potential Problem Area? Yes No Plot ID: B Explanation of atypical or problem area:
VEGETATION (For strata, indicate T = tree; S = shrub; H = herb; V = vine) Dominant Plant Species Stratum Dominant Plant Species Stratum 1 Yellow birch T 8 Bracken fern H 2 Red maple T 9 Wild sarsparilla H 3 Hay-scented fern H 10 4 Elderberry S 11 5 Blueberry S 12 6 Mayapple H 13 7 Yellow-poplar T 14 Hydrophytic Vegetation Indicators: % of Dominants that are OBL, FACW or FAC: 50% Check all indicators that apply & explain below:
Visual observation of plant species growing in areas Physiological/reproductive adaptations of prolonged inundation/saturation Wetland plant database Morphological adaptations Personal knowledge of regional plant communities Technical Literature Other (explain) Hydrophytic Vegetation Present? Yes No Rationale for decision/Remarks: Half wetland species but no indicators of growing with any innundation
HYDROLOGY Water Marks Oxidized Root Is it the growing season? Yes No Yes No Yes No On: (live root) Based on soil temp Channels <12 in. other Drainage Drift Lines Yes No Yes No (explain) Patterns Depth of inundation: inches FAC- Yes No Local Soil Yes No Neutral Survey Data Depth to free water in pit: None Inches Sediment Water-Stained Yes No Yes No Deposits Leaves Depth to saturated soil: None inches Other (explain): Check all that apply and explain below: Stream, Lake, or Gage Data Aerial Photographs Other
Hydrology Present? Yes No
Rationale for Dry, no indicators of higher water levels decision/Remarks:
214 SOILS
Chili Wooster Map Unit Name (Series): Drainage Class: Well drained complex Taxonomy: Field Observations Confirm Mapped Type? Yes No Profile Description:
Matrix color Mottle colors Mottle Depth Texture, concretions, Horizon (Munsell Moist) (Munsell Moist) abundance size contrast (inches) structure, etc. 0-3 O Leaf litter 3-7 A 10YR3/1 Clay loam 7+ B 10YR5/3 Sandy clay loam
Hydric Soil Indicators: (check all that apply) High Organic Content in Surface Layer of Sandy Histosol Reducing Conditions Soils Gleyed or Low-Chroma (=1) Histic Epipedon Organic Streaking in Sandy Soils Matrix Matrix Chroma with < 2 with Sulfidic Odor Listed on National/Local Hydric Soils List mottles Aquatic Moisture Mg or Fe Concretions Other (explain in remarks) Regime Hydric Soils Yes No Rationale for decision/Remarks: Dry, large rock pile present in transect
WETLAND DETERMINATION (Circle) Hydrophytic Vegetation Present? Yes No Is this Sampling Point Within a Yes No Wetland? Wetland Hydrology Present? Yes No Hydric Soils Present? Yes No Rationale/Remarks: No indicators of being within a wetland
NOTES:
215 DATA FORM (Revised) ROUTINE WETLAND DETERMINATION (1987 Corps Wetland Delineation Manual)
Project Site: Flatiron Lake Bog Date: June 12, 2008 Applicant/Owner: The Nature Conservancy County: Portage Investigator(s): Stephanie Colwell and Sandi Aupperle State: Ohio
Do Normal Circumstances exist on the site? Yes No Community ID: Flatiron Is the site significantly disturbed (atypical situation)? Yes No Transect ID: WD053 Is Area a Potential Problem Area? Yes No Plot ID: C Explanation of atypical or problem area:
VEGETATION (For strata, indicate T = tree; S = shrub; H = herb; V = vine) Dominant Plant Species Stratum Dominant Plant Species Stratum 1 Pignut hickory T 8 Flowering dogwood S 2 American beech T 9 Arrowwood S 3 Cucumber magnolia T 10 Yellow-poplar T 4 Bracken fern H 11 5 Mayapple H 12 6 Sugar maple T 13 7 Black cherry T 14 Hydrophytic Vegetation Indicators: % of Dominants that are OBL, FACW or FAC: 20% Check all indicators that apply & explain below:
Visual observation of plant species growing in areas Physiological/reproductive adaptations of prolonged inundation/saturation Wetland plant database Morphological adaptations Personal knowledge of regional plant communities Technical Literature Other (explain) Hydrophytic Vegetation Present? Yes No Rationale for decision/Remarks: Vegetation not wetland species primarily, no signs of growing with higher water levels
HYDROLOGY Water Marks Oxidized Root Is it the growing season? Yes No Yes No Yes No On: (live root) Based on soil temp Channels <12 in. other Drainage Drift Lines Yes No Yes No (explain) Patterns Depth of inundation: inches FAC- Yes No Local Soil Yes No Neutral Survey Data Depth to free water in pit: None Inches Sediment Water-Stained Yes No Yes No Deposits Leaves Depth to saturated soil: None inches Other (explain): Check all that apply and explain below: Stream, Lake, or Gage Data Aerial Photographs Other
Hydrology Present? Yes No
Rationale for No evidence of water near or at surface decision/Remarks:
216
SOILS
Chili-Wooster Map Unit Name (Series): Drainage Class: Well drained complex Taxonomy: Field Observations Confirm Mapped Type? Yes No Profile Description:
Matrix color Mottle colors Mottle Depth Texture, concretions, Horizon (Munsell Moist) (Munsell Moist) abundance size contrast (inches) structure, etc. 0-9 A 10YR4/2 Sandy loam 9+ B 10YR4/3 Sandy clay loam
Hydric Soil Indicators: (check all that apply) High Organic Content in Surface Layer of Sandy Histosol Reducing Conditions Soils Gleyed or Low-Chroma (=1) Histic Epipedon Organic Streaking in Sandy Soils Matrix Matrix Chroma with < 2 with Sulfidic Odor Listed on National/Local Hydric Soils List mottles Aquatic Moisture Mg or Fe Concretions Other (explain in remarks) Regime Hydric Soils Yes No Rationale for decision/Remarks: Soils dry with no indicators of water near surface
WETLAND DETERMINATION (Circle) Hydrophytic Vegetation Present? Yes No Is this Sampling Point Within a Yes No Wetland? Wetland Hydrology Present? Yes No Hydric Soils Present? Yes No Rationale/Remarks: No indicators of being in a wetland met
NOTES:
217