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Ecological site F093AY006MN

Depressional Wet Hardwood Forest

Last updated: 9/06/2024
Accessed: 11/21/2024

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General information

Approved. An approved ecological site description has undergone quality control and quality assurance review. It contains a working state and transition model, enough information to identify the ecological site, and full documentation for all ecosystem states contained in the state and transition model.

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Figure 1. Mapped extent

Areas shown in blue indicate the maximum mapped extent of this ecological site. Other ecological sites likely occur within the highlighted areas. It is also possible for this ecological site to occur outside of highlighted areas if detailed soil survey has not been completed or recently updated.

MLRA notes

Major Land Resource Area (MLRA): 093A–Superior and Rainy Stony and Rocky Till Plains and Moraines

The Superior Stony and Rocky Loamy Plains and Hills, Western Part is located and completely contained in northeastern Minnesota. This area has both the highest and lowest elevations in the state, as well as some of the state’s most rugged topography (Ojakangas and Matsch, 1982). The MLRA was glaciated by numerous advances of the Superior, Rainy, and Des Moines glacial lobes during the Wisconsin glaciation as well as pre-Wisconsin glacial periods. The geomorphic surfaces in this MLRA are geologically very young (i.e., 10,000 to 20,000 years) and dominated by drumlin fields, moraines, small lake plains, outwash plains, and bedrock-controlled uplands (USDA-NRCS, 2022).

There are thousands of lakes scattered throughout the region that were created by these glacial events. Most of these lakes are bedrock-controlled in comparison to adjacent glaciated regions where glacial drift deposits are much thicker and the lakes occur in depressions atop the glacial drift (Ojakangas and Matsch, 1982). In contrast to adjacent MLRAs, the depth to the predominantly crystalline or sandstone bedrock in MLRA 93A is relatively shallow because the most recent glacial events were more erosional than depositional (Ojakangas and Matsch, 1982).

Classification relationships

Major Land Resource Area (MLRA): Superior Stony and Rocky Loamy Plains and Hills, Western Part (93A)

USFS Subregions: Northern Superior Uplands Section (212L); North Shore Highlands Subsection (212Lb)

Ecological site concept

Depressional Wet Hardwood Forests are widespread throughout the distribution of the Superior Lobe glacial advance within MLRA 93A. These sites are developed primarily from low lying mineral soils, but can have up to sixteen inches (41 centimeters) of organic surface. They occur on small to moderate sized closed depressions and shallow, low gradient drainage networks, surrounded by an upland forest matrix. Later in the growing season ponded usually recedes, but they will again pond during moderate to heavy rainfall events. Hummocks from fallen trees create unique micro-topography, with micro-depressions that may hold water all year and adjacent root wads that shed water.

Relative to other forested wetland communities in the MLRA, Depressional Wet Hardwood Forests are comparatively richer, and have a diverse assemblage of ground flora. Wetland species are almost always present. Interestingly, the drier conditions on hummocks allow a number of common upland species to persist. In contrast, the adjacent wet micro-depressions often host obligate wetland species that are characteristic of more permanent wetlands.

Associated sites

F093AY013MN	Loamy Upland This ecological site is surrounded by upland soils and landforms. There are often rims of somewhat poorly and poorly drained soils of the same parent material adjacent to this site. In some cases, these are isolated depressions that are completely surrounded by a till upland mesic hardwood forest matrix. In other cases, shallow drainageways meander back-and-forth through many adjacent ecological sites.

F093AY013MN

Loamy Upland

This ecological site is surrounded by upland soils and landforms. There are often rims of somewhat poorly and poorly drained soils of the same parent material adjacent to this site. In some cases, these are isolated depressions that are completely surrounded by a till upland mesic hardwood forest matrix. In other cases, shallow drainageways meander back-and-forth through many adjacent ecological sites.

Similar sites

F093AY005MN	Wet Floodplain Soils wet layer depth is 0 - 15 inches (0 - 38 centimeters) and frequent flooding can occur in many areas. Dominant tree species include silver maple, black ash, green ash, and American elm.

F093AY005MN

Wet Floodplain

Soils wet layer depth is 0 - 15 inches (0 - 38 centimeters) and frequent flooding can occur in many areas. Dominant tree species include silver maple, black ash, green ash, and American elm.

Table 1. Dominant plant species

Tree	(1) Fraxinus nigra (2) Thuja occidentalis
Shrub	(1) Alnus incana (2) Acer spicatum
Herbaceous	(1) Glyceria striata (2) Caltha palustris

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Physiographic features

Wet Depressional Hardwood Forests are located on depressions, end moraines, ground moraines, outwash plains and inter-drumlins associated with the Automba and Nickerson phases of the Superior Lobe glacial advance (Table 2). The most common landforms are depressions (ponded or closed) and subtle, concave areas. They can also occur in shallow, low gradient drainageways that may receive concentrated flow (e.g., incipient drainage ways). Slope shape can be either linear or concave up slope, and is always concave across slope. Individual sites can be quite small in size, ranging from less than one acre, to ten acres.

These sites are ponded throughout the spring and early summer months, and generally dry out by August, and pond again in low to moderate rain events. During dry times the water table is generally within 10 inches, but can be as low as 24 inches. These sites receive very low to low runoff and lateral subsurface flow from adjacent, upslope ecological sites. They also produce very low to low runoff and lateral subsurface flow downslope, to streams, rivers, and large peatland basins. Elevation is mainly above 1,000 feet and below 1,600 feet.

Table 2. Representative physiographic features

Landforms	(1) Depression (2) Drainageway (3) Moraine (4) Closed depression (5) Outwash plain (6) Interdrumlin (7) Depression
Runoff class	Very low to low
Flooding frequency	None
Ponding duration	Brief (2 to 7 days) to very long (more than 30 days)
Ponding frequency	Occasional to frequent
Elevation	1,000 – 1,600 ft
Slope	1%
Ponding depth	6 in
Water table depth	24 in
Aspect	Aspect is not a significant factor

Climatic features

The average annual precipitation is 26-32 inches (66 to 81 centimeters). Measurable climatic variation (due to the lake effect) near some of Lake Superior may alter temperature and precipitation (Hillman & Nielsen, 2023). About 65 percent of the precipitation falls as rain during the growing season (May through September) and about 21 percent falls as snow. The freeze-free period averages about 130 days and ranges from 97 to 150 days (USDA-NRCS, 2022).

Table 3. Representative climatic features

Frost-free period (characteristic range)	88-109 days
Freeze-free period (characteristic range)	115-143 days
Precipitation total (characteristic range)	29-31 in
Frost-free period (actual range)	33-114 days
Freeze-free period (actual range)	66-150 days
Precipitation total (actual range)	26-32 in
Frost-free period (average)	90 days
Freeze-free period (average)	122 days
Precipitation total (average)	29 in

Characteristic range

Actual range

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Figure 2. Monthly precipitation range

Characteristic range

Actual range

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Figure 3. Monthly minimum temperature range

Characteristic range

Actual range

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Figure 4. Monthly maximum temperature range

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Figure 5. Monthly average minimum and maximum temperature

Figure 6. Annual precipitation pattern

Figure 7. Annual average temperature pattern

Climate stations used

(1) GRAND PORTAGE [USC00213296], Grand Portage, MN
(2) WOLF RIDGE ELC [USC00219134], Finland, MN
(3) DULUTH [USW00014913], Duluth, MN
(4) ELY 25E [USC00212555], Ely, MN
(5) KETTLE FALLS [USC00214306], Voyageurs Natl Park, MN
(6) KABETOGAMA [USC00214191], Orr, MN
(7) BRIMSON 2S [USC00210989], Brimson, MN

Influencing water features

These sites can be incipient drainage networks, with small perennial streams, or they can be in closed, isolated depressions. Seasonal ponding is most prominent during March through June and October through November. Water tables and water table recharge closely mimics annual rainfall graphs. They are either at or above the surface much of the year and may drop to a low of low of 12 inches (30 centimeters) during the dry months. In addition to precipitation inputs, these sites receive surface and subsurface water from surrounding sites. They also discharge water to lower elevation ecological sites, and ultimately to rivers, lakes, or large peatland basins.

In these relatively young morainic landscapes, well established dendritic drainage networks have not yet been developed. Instead, these sites exhibit water flow though after significant rainfall events. Landforms behave like closed depressions until an overflow threshold is achieved, wherein they begin to behave like drainageways. It is a complex interaction that is dependent upon factors like relative elevation and degree of incision. Stream orders associated with these sites are first, second, third, and fourth (SNF, unpublished report b). These sites also provide deep percolation for water table recharge.

Depressional Wet Hardwood Forests are classified as a Palustrine System, Forested Wetland Class, and depending on the State of vegetation, either a Broadleaf Deciduous or Dead Subclass, as described by Cowardin et al. (1979).

Wetland description

N/A

Soil features

The parent material for these soils includes loamy till, as well as outwash, from the Superior lobe glacial advance (Table 4). Although these are primarily mineral soils, up to 16 inches (41 centimeters) of organic parent material may be on the surface. On a given site, organic deposits (if existing) will be thickest near the center of the landform. In some cases there may be deeper organic surfaces that classify as true Histosols, but this is not typical condition of these landforms, and may be a relic of a past climatic or hydrologic time period. These soils are ponded, and as a result, are very poorly drained. However, wetness varies seasonally on these soils, which is a primary site factor defining this ecological site. Due to concave landforms and very poorly drained and ponded soils, soil textural classes are not a significant site factor for vegetation.

Surface texture is loam or sandy loam, and subsurface textures range from loam to very gravelly coarse sand. Soil pH on contributes to the rich nature of these plant communities, and ranges from 5.5 (moderately acid) to 6.5 (slightly acid), which is relatively high when compared to other wetland ecological sites in the MLRA. Soil orders are Inceptisols, and taxonomic classes are either Typic or Histic Humaquepts. Giese, Twig, Wahbegon, and Hulligan are all representative soil series for this ecological site.

Table 4. Representative soil features

Parent material	(1) Ablation till – gabbro (2) Outwash – sandstone (3) Lodgment till – basalt
Surface texture	(1) Very gravelly loam (2) Sandy loam
Family particle size	(1) Loamy
Drainage class	Very poorly drained
Permeability class	Slow to rapid
Soil depth	80 in
Surface fragment cover <=3"	1%
Surface fragment cover >3"	1%
Available water capacity (0-60in)	0.75 – 5 in
Soil reaction (1:1 water) (0-40in)	5.5 – 6.5
Subsurface fragment volume <=3" (Depth not specified)	8 – 65%
Subsurface fragment volume >3" (Depth not specified)	12%

Ecological dynamics

Seasonal variation in water table is the most important site factor defining Depressional Wet Hardwood Forests. Water tables limit the amount of oxygen available to plant roots; and oxygen levels determine the extent to which root respiration can take place, the level of organic litter decomposition, and the release of important nutrients for uptake by plants (MN DNR, 2011). Fires are not a significant disturbance factor in Depressional Wet Hardwood Forests in MLRA 93A. Instead, historic variability in vegetation structure was primarily related to small and moderate sized canopy openings produced from either dead/dying trees or mature and over mature windthrown trees (MN DNR, 2014; Landfire, 2007; Gucker, 2005). Currently, the dynamics of plant communities in this ecological site are similar to what they were historically. Although these sites are broadly distributed, they are generally small in size, and are part of a broader matrix of various upland forest types.

State and transition model

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Ecosystem states

1. Reference State - Mature Forest

2. Flooded State

3. Non-Forested State

T1A	-	Site becomes flooded
T1B	-	Tree canopy removed
T2A	-	Reduced water level
R3A	-	Forest succession
T3A	-	Increase in water levels

State 1 submodel, plant communities

1.1. Mature Forest

1.2. Young Forest

1.1.A	-	Disturbance; partial canopy removal
1.2.A	-	75 plus years without large-scale disturbance

State 2 submodel, plant communities

2.1. Open Water Wetland

State 3 submodel, plant communities

3.1. Shrub Swamp

3.2. Wet Meadow

3.1.A	-	Increase in ponding
3.2.A	-	Decreased ponding

State 1
Reference State - Mature Forest

Community phases within the Reference State are related to scattered small and moderate sized canopy openings from dead and/or windthrown trees. Windthrown trees are primarily dominant, above the canopy, and more exposed to wind events. These trees, with shallow root systems, were likely previously weakened by either excessive drought or ponding, leaving them open to attack by forest pests (MN DNR, 2014). Standing dead trees from excessive ponding or drought may also provide these canopy openings. An estimated rotation of such events is 110 years (MN DNR, 2014; MN DNR, 2005). This produced a patchwork of young and mature forests, all dominated by black ash. Black ash is fairly shade tolerant as a seedling, and is often the only advanced regeneration present in the understory, and thus it tends to replace itself in many situations (Gucker, 2005; Erdmann et al., 1987). Black ash is also a long-lived species and can live to over 250 years old (Gucker, 2005). Without larger openings, structure and composition of mature stands can be nearly perpetual, and gradually regenerate new trees via small, one to many tree sized openings. As a result of rather frequent, small scale openings, stands do not often become old growth (i.e., greater than 135 years; MN DNR, 2014). But in cases where they do, canopy structure is complex, and generally includes a component of long-lived and more shade tolerant white spruce and balsam fir. Northern white cedar and yellow birch often find their primary rooting substrate on downed woody debris associated with these openings. Both species regenerate well on mossy, rotting wood (i.e., nurse logs) that have consistent moisture (Smith, 2008 Erdmann, 1990; Johnston, 1990). Eventually, initial rooting media from downed woody debris can leave roots exposed to air and result in poorly formed trees. Northern white cedar can also regenerate by vegetation reproduction. These stems usually are developed from fallen trees and root from branches that come in contact with moist rooting media and are extremely shade tolerant (Erdmann, 1990). Hummocks and micro depressions resulting from windthrown trees are an important component of the Reference State. This variability in microsites provides opportunity for obligate wetland species in ponded micro depressions and upland species on the drier hummocks. Today, much of the distribution of this ecological site is in community phases very similar those in the Reference State.

Dominant plant species

black ash (Fraxinus nigra), tree
speckled alder (Alnus incana ssp. rugosa), shrub
mountain maple (Acer spicatum), shrub
bluejoint (Calamagrostis canadensis), grass
yellow marsh marigold (Caltha palustris), other herbaceous

Community 1.1
Mature Forest

Figure 8. Reference State (Community Phase 1.1 Mature Forest

Figure 9. Photo of a yellow birch with aerial roots, rooted

By stand age 75, a more characteristic, closed canopy and multi-tiered forest structure begins to develop (Table 8). Stands are initially dominated by black ash, but regeneration opportunities for northern white cedar, yellow birch, and white spruce begin to increase as the forest ages (Table 9). Also during this time, a build-up of down woody debris accumulates, as well as the characteristic hummocks and adjacent micro-depressions begin to increase micro-topography, and provide more sites for a diversity of ground flora species. Many sites will be essentially self-sustaining at this point, with periodic canopy openings keeping stands from attaining old growth status.

Dominant plant species

black ash (Fraxinus nigra), tree
speckled alder (Alnus incana ssp. rugosa), shrub
mountain maple (Acer spicatum), shrub
bluejoint (Calamagrostis canadensis), grass
yellow marsh marigold (Caltha palustris), other herbaceous

Table 5. Soil surface cover

Tree basal cover	1-10%
Shrub/vine/liana basal cover	4-13%
Grass/grasslike basal cover	9-15%
Forb basal cover	20-40%
Non-vascular plants	5-20%
Biological crusts	0%
Litter	10-30%
Surface fragments >0.25" and <=3"	0-1%
Surface fragments >3"	0-1%
Bedrock	0%
Water	1-3%
Bare ground	6-8%

Table 6. Woody ground cover

Downed wood, fine-small (<0.40" diameter; 1-hour fuels)	1-10%
Downed wood, fine-medium (0.40-0.99" diameter; 10-hour fuels)	1-8%
Downed wood, fine-large (1.00-2.99" diameter; 100-hour fuels)	1-5%
Downed wood, coarse-small (3.00-8.99" diameter; 1,000-hour fuels)	0-2%
Downed wood, coarse-large (>9.00" diameter; 10,000-hour fuels)	1-4%
Tree snags (hard*)	–
Tree snags (soft*)	–
Tree snag count (hard*)	20-80 per acre
Tree snag count (hard*)	10-30 per acre

* Decomposition Classes: N - no or little integration with the soil surface; I - partial to nearly full integration with the soil surface.

** >10.16cm diameter at 1.3716m above ground and >1.8288m height--if less diameter OR height use applicable down wood type; for pinyon and juniper, use 0.3048m above ground.

*** Hard - tree is dead with most or all of bark intact; Soft - most of bark has sloughed off.

Table 7. Canopy structure (% cover)

Height Above Ground (ft)	Tree	Shrub/Vine	Grass/ Grasslike	Forb
<0.5	0-1%	0-1%	1-5%	1-5%
>0.5 <= 1	1-5%	1-5%	5-25%	5-25%
>1 <= 2	5-10%	5-10%	25-50%	25-50%
>2 <= 4.5	5-40%	10-50%	5-15%	5-15%
>4.5 <= 13	10-40%	25-50%	–	–
>13 <= 40	25-50%	1-10%	–	–
>40 <= 80	35-65%	–	–	–
>80 <= 120	–	–	–	–
>120	–	–	–	–

Community 1.2
Young Forest

Figure 10. Reference State (Community Phase 1.2 Young Forest)

The initiation of stand development follows partial canopy loss by windthrow or canopy openings developed from pocket of dead trees. Black ash advanced regeneration is the dominant regenerating tree, but is accompanied by other hardwoods, such as paper birch, balsam poplar (Populus balsamea), or quaking aspen (Populus tremuloides). Increased light also favors some wetland shrubs and ground flora, particularly speckled alder and bluejoint. Co-dominant canopy trees generally reach a diameter of around eight inches before transitioning to a mature forest.

Dominant plant species

black ash (Fraxinus nigra), tree
paper birch (Betula papyrifera), tree
balsam fir (Abies balsamea), shrub
speckled alder (Alnus incana ssp. rugosa), shrub
Graminoid (grass or grass-like) (Graminoid (grass or grass-like)), grass

Pathway 1.1.A
Community 1.1 to 1.2

Mature Forest

Young Forest

Stand-levelling disturbance or small areas of partial canopy openings from wind or dead trees.

Pathway 1.2.A
Community 1.2 to 1.1

Young Forest

Mature Forest

Succession (75+ years without disturbance).

State 2
Flooded State

The Flooded State develops as a result of dammed or blocked waterways. Flooding is caused primarily by either beaver activity or development associated with road building. Only drainageway landforms are affected, and isolated depressions do not go through this state. Sites that have blocked water drainage from roads may become perpetual open water wetlands. In natural settings, the Flooded State can last for many years, but it ultimately depends on maintenance of high quality habitat conditions for beaver to proliferate. Once a site is abandoned, dams will gradually decline and ultimately drain, thereby beginning the transition to the Non-Forested State. Beaver populations in North America were drastically reduced by broad scale fur trapping during the Colonial time period, into the 1800s (Mitsch and Gosselink, 2007). As a result, natural conversion of these sites to the Flooded State may be less common today than it was prior to European settlement.

Dominant plant species

black ash (Fraxinus nigra), tree
speckled alder (Alnus incana ssp. rugosa), shrub
bluejoint (Calamagrostis canadensis), grass

Community 2.1
Open Water Wetland

Figure 11. Flooded State of a black ash depression, similar t

The only community phase in this state is characterized as having dead or dying overstory trees, flooded by up to several feet of essentially permanent water. Depending on depth of water, there will be areas with emergent aquatic vegetation, as well as scattered areas of marsh-like conditions.

Dominant plant species

black ash (Fraxinus nigra), tree
speckled alder (Alnus incana ssp. rugosa), shrub
bluejoint (Calamagrostis canadensis), grass

State 3
Non-Forested State

Sites can transition to this state by relatively sudden and complete loss of the tree canopy, thereby losing the transpiration of water from trees needed to keep water tables at bay and allow tree species to continually proliferate. This can happen as a result of intensive logging, forest pests, or general forest decline. This state will likely become common in the MLRA if the invasion of the exotic emerald ash borer (Agrilus planipennis) beetle is not halted (Slesak et al., 2014; Palik et al., 2012). Sites can also transition to this state from the Flooded State, following drainage of backed up water from beaver activity or road building. Initially, sites are wet meadows dominated by graminoids (e.g., bluejoint and sedges), eventually becoming invaded by wetland shrubs depending on level of ponding and soil saturation. These sites may have different soil characteristics depending on the extent and depth of sedimentation, which is largely dependent on how long the site was dammed (Naiman et al., 2005)and is also related to nearby land use and landscape-level soil geomorphology. More research is needed on how soil properties change following long term flooding from blocked hydrology. Other than a few scattered trees, these sites do not seem to regenerate trees well. Transition to the Reference State is relatively unknown, and will require long term ecological succession over the course of many decades. There is limited evidence that these communities succeed to a forested structure within a reasonable time frame (SNF, unpublished report b). Non-forested wetland conditions may persist for decades, and even centuries (Naiman et al., 2005; Terwilliger and Pastor, 1999). Viability of black ash seeds is only 8 years (Wright and Rauscher, 1990), so seeds are probably at least initially extirpated from the site. And since most sites are small and isolated, there may not be a reliable seed source nearby. The loss of important mycorrhizal relationships may also impede succession of forest trees. It has been shown that long-term flooding kills mycorrhizae that form essential relationships with tree species in other types of forested wetlands in the region, and recolonization following draining may be inhibited (Anderson and Fischer, 2015; Terwilliger and Pastor, 1999), which may be the case in this ecological site as well. All of this, in combination with extreme competition with resident vegetation, make succession to a forested state difficult.

Dominant plant species

speckled alder (Alnus incana ssp. rugosa), shrub
bluejoint (Calamagrostis canadensis), grass
sedge (Carex), grass

Community 3.1
Shrub Swamp

Figure 12. Non-Forested State similar to Community Phase 3.1 (MN DNR, 2005)

In this phase, shrubs are greater than 25% cover. Dominant species are speckled alder, redosier dogwood, and willows (Salix spp.). Bluejoint and a variety of sedges are also dominant, along with a myriad of sun-loving wetland forb species. There may be scattered trees as well, but they comprise low cover and are not significant to the overall structure of the plant community. With a continued lowering of the water table, it is possible for this phase to succeed to the Reference State if black ash and other trees can successfully establish.

Dominant plant species

speckled alder (Alnus incana ssp. rugosa), shrub
bluejoint (Calamagrostis canadensis), grass
sedge (Carex), grass

Community 3.2
Wet Meadow

Figure 13. Non-Forested State similar to community Phase 3.2 (MN DNR, 2005)

In this phase, shrubs are less than 25% cover. Bluejoint, sedges, and a variety of sun-loving wetland forbs dominate this phase. Lake sedge (Carex lacustris), the hummock-forming tussock sedge (C. stricta), and beaked sedge (C. utriculata) are the most common sedges, and can be dominant (MN DNR, 2005). The most common shrubs are speckled alder, redosier dogwood, and willows. There may be scattered trees as well, but they comprise low cover and are not significant to the overall structure of the plant community.

Dominant plant species

bluejoint (Calamagrostis canadensis), grass
sedge (Carex), grass

Pathway 3.1.A
Community 3.1 to 3.2

Shrub Swamp

Wet Meadow

Increased ponding, soil saturation.

Pathway 3.2.A
Community 3.2 to 3.1

Wet Meadow

Shrub Swamp

Decreased ponding, soil saturation.

Transition T1A
State 1 to 2

Flooding, backed up water from beaver dam or road bed.

Transition T1B
State 1 to 3

Removal of tree canopy resulting in loss of transpiration and elevated water levels.

Transition T2A
State 2 to 3

Drainage of open water.

Restoration pathway R3A
State 3 to 1

Long term forest succession.

Transition T3A
State 3 to 2

Flooding, backed up water from beaver dam or road bed.

Additional community tables

Table 8. Community 1.1 forest overstory composition

Common name	Symbol	Scientific name	Nativity	Height (ft)	Canopy cover (%)	Diameter (in)	Basal area (square ft/acre)
Tree
black ash	FRNI	Fraxinus nigra	Native	16–80	50–75	8–15	–
arborvitae	THOC2	Thuja occidentalis	Native	16–50	5–25	12–20	–
yellow birch	BEAL2	Betula alleghaniensis	Native	16–40	5–25	5–10	–
balsam fir	ABBA	Abies balsamea	Native	16–40	1–5	3–8	–
white spruce	PIGL	Picea glauca	Native	16–40	1–5	3–8	–

Table 9. Community 1.1 forest understory composition

Common name	Symbol	Scientific name	Nativity	Height (ft)	Canopy cover (%)
Grass/grass-like (Graminoids)
fowl mannagrass	GLST	Glyceria striata	Native	0.1–3	10–50
bluejoint	CACA4	Calamagrostis canadensis	Native	0.1–3	10–50
bluejoint	CACA4	Calamagrostis canadensis	Native	0.1–3	10–50
bristlystalked sedge	CALE10	Carex leptalea	Native	0.1–2	5–15
greater bladder sedge	CAIN12	Carex intumescens	Native	0.1–2	1–10
awlfruit sedge	CAST5	Carex stipata	Native	0.1–1	1–10
graceful sedge	CAGR2	Carex gracillima	Native	0.1–1	1–10
softleaf sedge	CADI6	Carex disperma	Native	0.1–1	1–10
fringed brome	BRCI2	Bromus ciliatus	Native	0.1–2	1–5
Forb/Herb
yellow marsh marigold	CAPA5	Caltha palustris	Native	0.1–1	10–50
northern bugleweed	LYUN	Lycopus uniflorus	Native	0.1–1	5–25
dwarf red blackberry	RUPU	Rubus pubescens	Native	0.1–1	5–15
blue skullcap	SCLA2	Scutellaria lateriflora	Native	0.1–1	5–15
touch-me-not	IMPAT	Impatiens	Native	0.1–3	5–15
purplestem aster	SYPUP	Symphyotrichum puniceum var. puniceum	Native	0.1–3	5–15
parasol whitetop	DOUMU	Doellingeria umbellata var. umbellata	Native	0.1–3	1–10
wild sarsaparilla	ARNU2	Aralia nudicaulis	Native	0.1–2	1–5
starflower	TRBO2	Trientalis borealis	Native	0.1–1	1–5
arctic sweet coltsfoot	PEFR5	Petasites frigidus	Native	0.1–1	1–5
spotted joe pye weed	EUMA9	Eutrochium maculatum	Native	0.1–3	1–5
naked miterwort	MINU3	Mitella nuda	Native	0.1–1	1–5
harlequin blueflag	IRVE2	Iris versicolor	Native	0.1–2	1–5
tall bluebells	MEPA	Mertensia paniculata	Native	0.1–1	1–5
woodland horsetail	EQSY	Equisetum sylvaticum	Native	0.1–1	1–5
threeleaf goldthread	COTR2	Coptis trifolia	Native	0.1–1	1–5
Jack in the pulpit	ARTR	Arisaema triphyllum	Native	0.1–2	1–5
small enchanter's nightshade	CIAL	Circaea alpina	Native	0.1–1	1–5
giant goldenrod	SOGI	Solidago gigantea	Native	0.1–3	1–5
eastern swamp saxifrage	SAPE8	Saxifraga pensylvanica	Native	0.1–2	1–5
wood anemone	ANQU	Anemone quinquefolia	Native	0.1–1	1–5
Canada mayflower	MACA4	Maianthemum canadense	Native	0.1–1	1–5
bunchberry dogwood	COCA13	Cornus canadensis	Native	0.1–1	1–5
purple meadow-rue	THDA	Thalictrum dasycarpum	Native	0.1–3	1–2
Fern/fern ally
common ladyfern	ATFI	Athyrium filix-femina	Native	0.1–2	5–25
intermediate woodfern	DRIN5	Dryopteris intermedia	Native	0.1–1	5–15
sensitive fern	ONSE	Onoclea sensibilis	Native	0.1–2	5–15
western oakfern	GYDR	Gymnocarpium dryopteris	Native	0.1–1	1–5
ostrich fern	MAST	Matteuccia struthiopteris	Native	0.1–3	1–5
long beechfern	PHCO24	Phegopteris connectilis	Native	0.1–1	1–5
Shrub/Subshrub
speckled alder	ALINR	Alnus incana ssp. rugosa	Native	1–16	25–75
redosier dogwood	COSE16	Cornus sericea	Native	1–10	1–15
beaked hazelnut	COCO6	Corylus cornuta	Native	1–10	1–15
American fly honeysuckle	LOCA7	Lonicera canadensis	Native	1–5	1–5
American cranberrybush	VIOPA2	Viburnum opulus var. americanum	Native	1–5	1–5
red currant	RITR	Ribes triste	Native	1–5	1–5
Tree
mountain maple	ACSP2	Acer spicatum	Native	1–16	5–25
American red raspberry	RUID	Rubus idaeus	Native	1–10	1–15
black ash	FRNI	Fraxinus nigra	Native	1–10	1–15
chokecherry	PRVI	Prunus virginiana	Native	1–10	1–5

Supporting information

Inventory data references

A total of 12 integrated plots, ranging from Tier 2 to Tier 3 intensity, were used as a basis for this ecological site. Three of these were Type Locations representing the data-supported Community Phase 1.1 in the state-and-transition model, and included all necessary data elements for a Tier 3 dataset. No other community phases were supported with quantitative data analysis. All 12 plots had soil pedon and site data collected by a professional soil scientist using a form equivalent to SF-232. Pits were hand-dug using spade shovels, sharpshooters, and/or bucket augers. Of the 12 plots, two were located at established MN DNR relevé points, obtained and used with permission from the MN DNR County Biological Survey. List of MN DNR relevé plots used with verified soils data: 3475 and 8301.

Other references

Anderson, C.E. and Adelheid Fischer 2015. North Shore: A Natural History of Minnesota’s Superior Coast. University of Minnesota Press. Minneapolis, MN.

Carmean, W.H. 1978. Site Index Curves for Northern Hardwoods in Northern Wisconsin and Upper Michigan. USDA For. Serv. Research Paper NC-160. St. Paul, MN.

Carmean, W.H., J.T. Hahn, and R.D. Jacobs. 1989. Site Index Curves for Forest Tree Species in the Eastern United States. USDA For. Serv. Gen. Tech. Rep. NC-128. St. Paul, MN.

Cowardin, L. M., V. Carter, F. C. Golet, and E.T. LaRoe. 1979. Classification of Wetlands and Deepwater Habitats of the United States. FWS/OBS-79/31, U.S. Department of Interior-Fish and Wildlife Service, Washington, D.C.

Erdmann, G.G. 1990. Yellow Birch. In: Silvics of North America, Vol 2, Burns, R.M., and B.H. Honkala (tech cords). USDA For. Serv. Handb. 654, Washington, DC.

Erdmann, G.G., T.R. Crow, R.M. Peterson, Jr., and C.D. Wilson. 1987. Managing Black Ash in the Lake States. USDA For. Serv. Gen. Tech. Rep., NC-115.

Flaccus, E. and L.F. Ohmann. 1964. Old-growth Northern Hardwood Forests in Northeastern Minnesota. Ecology 45:3, 448-459.

Gucker, C.L. 2005. Fraxinus nigra. In: Fire Effects Information System, [Online]. USDA For. Serv. Rocky Mountain Research Station, Fire Sciences Laboratory. Available online at http://www.fs.fed.us/database/feis/; last accessed January 3, 2014.

Hillman, A., & Nielsen, S. E. (2023). Lake Superior’s summer cooling of shorelines and adjacent inland forests: Implications for refugia of boreal forests and disjunct Arctic–Alpine plants. Ecology and Evolution, 13(12). doi:10.1002/ece3.10833

Johnston, W.F. 1990. Northern White Cedar. In: Silvics of North America, Vol 2, Burns, R.M., and B.H. Honkala (tech cords). USDA For. Serv. Handb. 654, Washington, DC.

Landfire. 2007. Biophysical Setting 4114810 Laurentian-Acadian Alkaline Conifer-Hardwood Swamp. In: Landfire National Vegetation Dynamics Models. USDA For. Serv. and U.S. Department of Interior. Washington, DC.

Minnesota Department of Natural Resources. 2014. WFn64 – Northern Very Wet Ash Swamp: Natural Disturbance Regime, Stand Dynamics, and Tree Behavior. Available online at http://files.dnr.state.mn.us/forestry/ecssilviculture/plantcommunities/WFn64.pdf; last accessed November 11, 2014.

Minnesota Department of Natural Resources. 2013a. Climate – Frequently Asked Questions. Available online at http://www.dnr.state.mn.us/climate/faqs.html; last accessed December 11, 2013.

Minnesota Department of Natural Resources. 2011. Ash Management Guidelines for Private Forest Landowners. University of Minnesota Extension. St. Paul, MN.

Minnesota Department of Natural Resources. 2005. Field Guide to the Native Plant Communities of Minnesota: the Laurentian Mixed Forest Province. Ecological Land Classification Program, Minnesota County Biological Survey, and Natural Heritage and Nongame Research Program. St. Paul, Minnesota.

Minnesota Division of Forestry. 2013. Minnesota Department of Natural Resources Tamarack Assessment Project. Available online at http://files.dnr.state.mn.us/forestry/ecssilviculture/policies/tamarackAssessmentProject2013.pdf; last accessed November 11, 2014.

Mitsch, WJ. and J.G. Gosselink. 2007. Wetlands, fourth ed. John Wiley & Sons, Inc. New York, NY.

Naiman, R.J., H. Dècamps, and M.E. McClain. 2005. Riparia: Ecology, Conservation, and Management of Streamside Communities. Elsevier Academic Press. San Diego, CA.

NatureServe. 2013a. Associations and Alliances of USFS Section 212L in Minnesota. NatureServe, St. Paul, Minnesota.

NatureServe. 2013b. Ecological Systems of USFS Section 212L in Minnesota. NatureServe, St. Paul, Minnesota.

Ojakangas, R.W. and C.L. Matsch. 1982. Minnesota’s Geology. University of Minnesota Press. Minneapolis, MN.

Palik, B.J., M.E. Ostry, R.C. Venette, and E. Abdela. 2012. Tree Regeneration in Black Ash (Fraxinus nigra) Stands Exhibiting Crown Dieback in Minnesota. Forest Ecol. Mgmt. 269: 26-30.

Slesak, R.A., C.F. Lenhart, K.N. Brooks, D.W. D'Amato, and B.J. Palik. 2014. Water Table Response to Harvesting and Simulated Emerald Ash Borer Mortality in Black Ash Wetlands in Minnesota, USA. Can. J. Forest Res. 44:961-968.

Smith, W.R. 2008. Trees and Shrubs of Minnesota. University of Minnesota Press. Minneapolis, MN.

Superior National Forest. Unpublished report(a).
Superior National Forest Ecological Landtype Descriptions. USDA For. Serv. Duluth, Minnesota.

Superior National Forest. Unpublished report(b). Superior National Forest Ecological Landtype Phase Descriptions. USDA For. Serv. Duluth, Minnesota.

Terwilliger, J. and J. Pastor. 1999. Small Mammals, Ectomycorrhizae, and Conifer Succession in Beaver Meadows. Oikos 85: 83–94.
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Natural Resources Conservation Service. 2006. Land Resource Regions and Major Land Resource Areas of the United States, the Caribbean, and the Pacific Basin. USDA Handbook 296. Washington, DC.

Wright, J.W. and H.M. Rauscher. 1990. Black Ash. In: Silvics of North America, Vol 2, Burns, R.M., and B.H. Honkala (tech cords). USDA For. Serv. Handb. 654, Washington, DC.

Contributors

Kyle Steele, Former NRCS Ecologist, Albert Lea, MN
Roger Risely, Former SSOL, Duluth, MN
Kade Anderson, NRCS Ecologist, Duluth, MN

Approval

Suzanne Mayne-Kinney, 9/06/2024

Rangeland health reference sheet

Interpreting Indicators of Rangeland Health is a qualitative assessment protocol used to determine ecosystem condition based on benchmark characteristics described in the Reference Sheet. A suite of 17 (or more) indicators are typically considered in an assessment. The ecological site(s) representative of an assessment location must be known prior to applying the protocol and must be verified based on soils and climate. Current plant community cannot be used to identify the ecological site.

Author(s)/participant(s)
Contact for lead author
Date	09/07/2024
Approved by	Suzanne Mayne-Kinney
Approval date
Composition (Indicators 10 and 12) based on	Annual Production

Indicators

Number and extent of rills:
Presence of water flow patterns:
Number and height of erosional pedestals or terracettes:
Bare ground from Ecological Site Description or other studies (rock, litter, lichen, moss, plant canopy are not bare ground):
Number of gullies and erosion associated with gullies:
Extent of wind scoured, blowouts and/or depositional areas:
Amount of litter movement (describe size and distance expected to travel):
Soil surface (top few mm) resistance to erosion (stability values are averages - most sites will show a range of values):
Soil surface structure and SOM content (include type of structure and A-horizon color and thickness):
Effect of community phase composition (relative proportion of different functional groups) and spatial distribution on infiltration and runoff:
Presence and thickness of compaction layer (usually none; describe soil profile features which may be mistaken for compaction on this site):
Functional/Structural Groups (list in order of descending dominance by above-ground annual-production or live foliar cover using symbols: >>, >, = to indicate much greater than, greater than, and equal to):

Dominant:

Sub-dominant:

Other:

Additional:
Amount of plant mortality and decadence (include which functional groups are expected to show mortality or decadence):
Average percent litter cover (%) and depth ( in):
Expected annual annual-production (this is TOTAL above-ground annual-production, not just forage annual-production):
Potential invasive (including noxious) species (native and non-native). List species which BOTH characterize degraded states and have the potential to become a dominant or co-dominant species on the ecological site if their future establishment and growth is not actively controlled by management interventions. Species that become dominant for only one to several years (e.g., short-term response to drought or wildfire) are not invasive plants. Note that unlike other indicators, we are describing what is NOT expected in the reference state for the ecological site:
Perennial plant reproductive capability: